Nuclear ScienceUnlocking the Hidden Value of Nuclear Fuel:The Societal Benefits of Diverse Material Recycling© OECD 2024NEA No. 7674NUCLEAR ENERGY AGENCYORGANISATION FOR ECONOMIC CO-OPERATION AND DEVELOPMENTORGANISATION FOR ECONOMIC CO-OPERATION AND DEVELOPMENTThe OECD is a unique forum where the governments of 38 democracies work together to address the economic, social and environmental challenges of globalisation. The OECD is also at the forefront of efforts to understand and to help governments respond to new developments and concerns, such as corporate governance, the information economy and the challenges of an ageing population. 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The opinions expressed and arguments employed herein do not necessarily reflect the officialviews of the member countries of the OECD or its Nuclear Energy Agency.NUCLEAR ENERGY AGENCYThe OECD Nuclear Energy Agency (NEA) was established on 1 February 1958. Current NEA membership consists of 34 countries: Argentina, Australia, Austria, Belgium, Bulgaria, Canada, Czechia, Denmark, Finland, France, Germany, Greece, Hungary, Iceland, Ireland, Italy, Japan, Korea, Luxembourg, Mexico, the Netherlands, Norway, Poland, Portugal, Romania, Russia (suspended), the Slovak Republic, Slovenia, Spain, Sweden, Switzerland, Türkiye, the United Kingdom and the United States. The European Commission and the International Atomic Energy Agency also take part in the work of the Agency.The mission of the NEA is:to assist its member countries in maintaining and further developing, through international cooperation, the scientific, technological and legal bases required for the safe, environmentally sound and economical use of nuclear energy for peaceful purposes.to provide authoritative assessments and to forge common understandings on key issues as input to government decisions on nuclear energy policy and to broader OECD analyses in areas such as energy and the sustainable development of low-carbon economies.Specific areas of NEA competence include the safety and regulation of nuclear activities, radioactive waste management, radiological protection, nuclear science, economic and technical analyses of the nuclear fuel cycle, nuclear law and liability, and public information. 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If using such material, you are responsible for obtaining permission from the third party and for any claims of infringement.You must not use the OECD logo, visual identity or cover image without express permission or suggest the OECD endorses your use of the work.Any dispute arising under this licence shall be settled by arbitration in accordance with the Permanent Court of Arbitration (PCA) Arbitration Rules 2012. The seat of arbitration shall be Paris (France). The number of arbitrators shall be one.Cover photos: llustration of the waste hierarchy; (Am,U)O2 prototype pellet and prototype disc (Courtesy of the EC Joint Research Centre); Illustration of photo-reduction for PGM recovery (Reproduced from Li et al., 2017). ForewordUnder the auspices of the Nuclear Energy Agency (NEA)’s Nuclear Science Committee (NSC), the Working Party on Scientific Issues of Advanced Fuel Cycles (WPFC) was established to coordinate scientific activities related to advanced nuclear fuel cycles, including fuel cycle scenarios, innovative fuels and materials, separation chemistry, waste disposal and coolant technologies. Various expert groups have been established to cover the topics mentioned above. The Expert Group on Fuel Recycling and Waste Technology (EGFRW) – previously known as the Expert Group on Fuel Recycling Chemistry (EGFRC) – was created in 2012 and focuses on the separation processes relevant to recycling technologies for spent nuclear fuel including reprocessing, waste treatment, recycling and reuse of spent fuel components but excluding long-term (dry/wet) spent fuel storage technologies. After publishing its State-of-the-art Report on the Progress of Nuclear Fuel Cycle Chemistry, the Expert Group initiated a complementary review of the potential for recycling and reusing materials from spent nuclear fuels other than actinides for fuels or transmutation. The study primarily focused on technologies deployed or under research and development in the NEA member countries. This report presents the results of that study.AcknowledgementsThe NEA acknowledges the significant contributions of the members of the Expert Group on Fuel Recycling and Waste Technology (EGFRW) in drafting this report. Particular appreciation is expressed for the contributions of Mark Sarsfield (National Nuclear Laboratory, United Kingdom), Daniel Freis (Joint Research Centre, European Commission), Ben Hodgson (National Nuclear Laboratory, United Kingdom) and Praveen K. Thallapally (Pacific Northwest National Laboratory, United States).Thanks are also due to the members of the Expert Group and other invited international experts for reviewing the report.Contributing authorsFranceStéphane BOURG (OFREMI, formerly CEA)JapanTatsuro MATSUMURA (JAEA)Russian FederationAnzhelika KHAPERSKAIA (Rosatom until February 2021, then IAEA)United KingdomSteve PALETHORPE (NNL)Robin TAYLOR (NNL), Chair of the EGFRWUnited StatesEmory COLLINS (ORNL)Bill DELCUL (DOE)Jack LAW (INL, retired)Gregg LUMETTA (PNNL)European CommissionPavel SOUČEK (JRC)NEAStéphanie CORNET, former Technical Secretariat (until October 2020)Gabriele GRASSI, Technical Secretariat Table of contents TOC \o "1-2" \h \z \u List of abbreviations and acronyms PAGEREF _Toc168996975 \h 9Executive summary PAGEREF _Toc168996976 \h 131. Introduction PAGEREF _Toc168996977 \h 151.1. Context PAGEREF _Toc168996978 \h 151.2. Motivation PAGEREF _Toc168996979 \h 161.3. Scope PAGEREF _Toc168996980 \h 171.4. References PAGEREF _Toc168996981 \h 172. Background PAGEREF _Toc168996982 \h 192.1. Spent fuel characteristics PAGEREF _Toc168996983 \h 192.2. Potentially recoverable materials PAGEREF _Toc168996984 \h 222.3. Demand for materials PAGEREF _Toc168996985 \h 242.4. Critical materials to target for recovery from recycling SNF PAGEREF _Toc168996986 \h 252.5. References PAGEREF _Toc168996987 \h 253. Actinides PAGEREF _Toc168996988 \h 273.1. Neptunium PAGEREF _Toc168996989 \h 273.2. Americium PAGEREF _Toc168996990 \h 313.3. References PAGEREF _Toc168996991 \h 404. Group 1 and 2 elements PAGEREF _Toc168996992 \h 434.1. Caesium PAGEREF _Toc168996993 \h 434.2. Strontium PAGEREF _Toc168996994 \h 444.3. References PAGEREF _Toc168996995 \h 455. Noble gases PAGEREF _Toc168996996 \h 475.1. Xenon PAGEREF _Toc168996997 \h 475.2. Krypton PAGEREF _Toc168996998 \h 495.3. References PAGEREF _Toc168996999 \h 506. Platinum group metals PAGEREF _Toc168997000 \h 516.1. Palladium PAGEREF _Toc168997001 \h 536.2. Ruthenium PAGEREF _Toc168997002 \h 536.3. Rhodium PAGEREF _Toc168997003 \h 546.4. ImPACT PAGEREF _Toc168997004 \h 576.5. References PAGEREF _Toc168997005 \h 587. Rare earth elements PAGEREF _Toc168997006 \h 617.1. Recovery of lanthanides PAGEREF _Toc168997007 \h 627.2. References PAGEREF _Toc168997008 \h 688. Zirconium recovery PAGEREF _Toc168997009 \h 718.1. Zircalloy cladding recovery and reuse PAGEREF _Toc168997010 \h 718.2. Zircaloy recovery from existing hydrometallurgical separations PAGEREF _Toc168997011 \h 728.3. References PAGEREF _Toc168997012 \h 749. Industrial applications of isotopes PAGEREF _Toc168997013 \h 779.1. Introduction PAGEREF _Toc168997014 \h 779.2. Isotope production PAGEREF _Toc168997015 \h 779.3. Industrial applications PAGEREF _Toc168997016 \h 799.4. References PAGEREF _Toc168997017 \h 8210. Medical applications of isotopes PAGEREF _Toc168997018 \h 8510.1. References PAGEREF _Toc168997019 \h 8711. Hardware component recycle PAGEREF _Toc168997020 \h 8911.1. References PAGEREF _Toc168997021 \h 8912. Summary and future perspectives PAGEREF _Toc168997022 \h 9112.1. Summary PAGEREF _Toc168997023 \h 9112.2. Perspective PAGEREF _Toc168997024 \h 93List of figures TOC \h \z \t "Figure Title" \c 2.1. Average weight composition, PWR and BWR fuel, accumulated from 1968 to 2002 PAGEREF _Toc168997061 \h 202.2. Suggested roadmap of anticipated future fuel cycle to promote the sustainability of nuclear energy systems PAGEREF _Toc168997062 \h 212.3. Illustration of the waste hierarchy PAGEREF _Toc168997063 \h 222.4. Mass of nuclides against atomic mass for 10 years cooled, 50 GWd/tHM burn-up MOX fuel PAGEREF _Toc168997064 \h 233.1. Transmutation path for production of 238Pu from 237Np PAGEREF _Toc168997065 \h 283.2. 238Pu production process PAGEREF _Toc168997066 \h 283.3. SRS 238Pu separation process PAGEREF _Toc168997067 \h 293.4. Overall ORNL chemical processing scenario PAGEREF _Toc168997068 \h 303.5. Example calculation of build-up of 241Am in reprocessed Pu from UO2 and MOX irradiation PAGEREF _Toc168997069 \h 333.6. Phase diagram of the Am-O system PAGEREF _Toc168997070 \h 343.7. The AMPPEX process for separation of 241Am from aged PuO2 PAGEREF _Toc168997071 \h 363.8. (Am,U)O2 prototype pellet and prototype disc PAGEREF _Toc168997072 \h 383.9. Crystallographic swelling of (Am,U)O2 under the effect of alpha self-irradiation and weight change during oxidation test on (Am,U)O1.8 PAGEREF _Toc168997073 \h 385.1. Production and uses of xenon PAGEREF _Toc168997074 \h 476.1. Illustration of photo-reduction for PGM recovery PAGEREF _Toc168997075 \h 577.1. Lanthanide separation from the minerals cerite and ytterbite using fractional crystallisation techniques PAGEREF _Toc168997076 \h 627.2. Original TALSPEAK flowsheet for purification of americium and curium PAGEREF _Toc168997077 \h 637.3. Schematic of the EURO-GANEX cycle PAGEREF _Toc168997078 \h 658.1. Potential insertion of recycled zirconium into the process for zircaloy cladding manufacture PAGEREF _Toc168997079 \h 718.2. Schematic illustration of the process steps in the thionyl chloride zircaloy purification scheme PAGEREF _Toc168997080 \h 738.3. Schematic of the thionyl chloride chemical decladding PAGEREF _Toc168997081 \h 74List of tables TOC \f A \h \z \t "Table Title" \c 2.1. Recoverable components in spent nuclear fuel PAGEREF _Toc169010244 \h 222.2. EU categorisation of rare earth elements PAGEREF _Toc169010245 \h 243.1. Typical isotopic composition of Pu in spent nuclear fuel at the end of irradiation PAGEREF _Toc169010246 \h 333.2. Properties of 241Am and 238Pu as metal and oxide PAGEREF _Toc169010247 \h 343.3. Composition of the solution entering the chromatographic stage PAGEREF _Toc169010248 \h 396.1. Isotopic composition of fission product PGMs in spent fuel PAGEREF _Toc169010249 \h 529.1. Isotopes used for radioactive tracing and non-destructive testing PAGEREF _Toc169010250 \h 799.2. Industrial radioisotope half-lives, quantities and uses PAGEREF _Toc169010251 \h 8210.1. Medical radioisotope half-lives, quantities and uses PAGEREF _Toc169010252 \h 8610.2. Quantity of medical target radioisotopes in spent nuclear fuel (SNF) PAGEREF _Toc169010253 \h 87List of abbreviations and acronymsAHAAcetohydroxamic acid AMPPEXAmericium and plutonium purification by extraction ANSTOAustralian Nuclear Science and Technology Organisation ATRAdvanced test reactorBNWLBattelle Northwest Laboratory (United States)BR-2Belgian reactor 2BWRBoiling water reactor CANDUCanada Deuterium UraniumCaSDBCalcium–4,4'–sulfonyl dibenzoateCCD-PEGChlorinated cobalt dicarbolide-polyethylene glycolCEAFrench Alternative Energies and Atomic Energy Commission CEPCaesium Extraction Plant CHALMEXChalmers extraction CHONCarbon, hydrogen, oxygen, and nitrogen atomsDCCDisplacement complexing chromatography DEHiBAN,N-di-(ethyl-2-hexyl)isobutyramideDGRDeep geological repositoryDHOAN,N′-dihexyloctanamide DIAMEX-SANEXDiamide extraction - selective actinide extractionDIPBDiisopropylbenzeneDMDOHEMAN,N’-dimethyl-N,N’-dioctyl-2-(2-hexyloxyethyl)-malonamide DTPADiethylenetriaminepentaacetate EASACEuropean Academies’ Science Advisory CouncilEDTAEthylenediaminetetraacetate EGFRCExpert Group on Fuel Recycling Chemistry (NEA)EGFRWExpert Group on Fuel Recycling and Waste Technology (NEA)ESAEuropean Space Agency ETRR-2Egyptian Second Research ReactorEUEuropean UnionFAOFood and Agriculture Organization of the United NationsFPFission productFPEXFission product extractionGANEXGrouped actinide extraction GWdGigawatt-daysHALEUHigh assay low-enriched uraniumHDEHPDi-2-ethylhexyl phosphoric acid HEDTAN-(2-hydroxyethyl)ethylenediamine-N, N’, N’-triacetic acid HEH[EHP]2-ethylhexylphosphonic acid mono-2-ethylhexyl ester HFRHigh flux reactorHFETRHigh flux engineering test reactorHFRLMHollow fibre renewable liquid membrane HLLWHigh-level liquid wasteHLWHigh-level wasteIAEAInternational Atomic Energy Agency ImPACTImpulsing Paradigm Change through Disruptive TechnologiesINLIdaho National Laboratory (United States)IRENational Institute for Radioelements (Belgium)i-SANEXInnovative-selective actinide extractionJRCJoint Research Centre (Belgium)LALactic acidLLFPLong-lived fission products Ln LanthanideLWRLight water reactorLWRHULight weight radioisotope heater unit MAMinor actinidesMOFMetal organic frameworks MOXMixed oxideMSRMolten salt reactorNEANuclear Energy Agency NNLNational Nuclear Laboratory (United Kingdom)NOxNitrogen oxideNSCNuclear Science Committee (NEA)OECDOrganisation for Economic Co-operation and Development OKOdourless KeroseneOPALOpen Pool Australian Light water reactor ORNLOak Ridge National Laboratory (United States)P&TPartitioning and transmutationPGMPlatinum group metalsPNNLPacific Northwest National Laboratory (United States)POCPorous organic cages PUREXPlutonium uranium reduction extraction (process)PWRPressurised water reactor R&DResearch and developmentREDCRadiochemical Engineering Development Center REERare earth elementsRHURadioisotope heater units RPSRadioisotope power systems RTGRadioisotope thermoelectric generators SDBSulfonyldibenzoateSNFSpent nuclear fuelSO3-Ph-BTPSulphonated bis-triazinyl pyridine SREXStrontium extraction SRLSavannah River Laboratory (United States)SRSSavannah River Site TALSPEAKTrivalent Actinide Lanthanide Separation by Phosphorus reagent Extraction from Aqueous ComplexationTBPTributyl phosphatetHMTonnes heavy metalTHOREXThorium extractionTHPSPhosphorothioic-triamideTODGAN,N,N′,N′ tetraoctyl diglycolamideTRUTransuranic or TransuraniumTTCTwice-through cycleUKUnited KingdomUOXUranium oxideUREXUranium extractionUSUnited StatesUSDUS dollarUS-DOEUnited States Department of EnergyWHOWorld Health OrganizationWPFCWorking Party on Scientific Issues of Advanced Fuel Cycles (NEA)ZIRCEXHybrid zirconium extractionExecutive summaryIn 2018, the Expert Group on Fuel Recycling and Waste Technology (EGFRW), under the auspices of the Working Party on Scientific Issues of Advanced Fuel Cycles (WPFC) of the Nuclear Sciences Committee (NSC) of the Nuclear Energy Agency (NEA), published a State-of-the-art Report on the Progress of Nuclear Fuel Cycle Chemistry (NEA, 2018). This report reviewed the range of separation processes that are under development internationally to reprocess and recycle nuclear materials in future closed nuclear fuel cycles. The advantages of recycling nuclear fuel are that it extends the natural uranium resources, reduces the burden of radioactive waste for geological disposal (the volume and radiotoxicity of the waste and the size of the repository) and reduces the overall environmental impact of nuclear energy. During this work, the EGFRW identified an additional opportunity: recycling other materials from spent nuclear fuels that can have societal benefits beyond reuse as new nuclear fuels, such as in medical, space or other industrial applications or as critical element supplies. This can include recycling structural materials and would further reduce the overall waste burden. Therefore, the EGFRW undertook an activity to review the potential for recycling and reusing these other materials from spent nuclear fuels. The approach taken was that the members of the EGFRW reviewed the published literature to understand the state of the art, with a specific focus on developments in the NEA member countries.While this is not a new concept, with such efforts going back to the earliest days of the nuclear industry, it is an issue of increasing importance. Industrial activities are increasingly analysed in terms of their sustainability, which is usually seen as the confluence of environmental, economic and societal impacts. The concept of the circular economy also fits into this view, where the intention is to repurpose, reuse or recycle materials in the economy as far as possible to minimise the use of natural resources and the waste generated by economic activities. Making the most of the materials contained within spent fuel by recycling them rather than direct disposal of spent fuel (the so-called “open” fuel cycle) is consistent with these trends. More specifically, the security of supply of so-called critical materials (e.g. rare earth elements, platinum group metals), which are essential to many modern technologies, has become a concern. There are also needs for radioisotopes for medical use, space power and other industries. Some of these also have supply problems.While the recovery of these materials from spent nuclear fuels has been done in the past, it has generally been considered either too difficult and/or uneconomic to do at scale. Still, questions of technical feasibility and economics change over time with shifts in geopolitical situations, societal or cultural issues and technological progress. Furthermore, the recovery of materials for non-nuclear (e.g. medical) applications as well as the reduction in the radioactive waste burden could have a significant positive impact on public acceptance of nuclear energy.It is therefore timely to reassess the potential of recycling and reusing components from spent nuclear fuel for uses other than as nuclear fuel in reactors or accelerator-driven systems.This report provides an introduction to key concepts, including the motivation for such work and relevant technical background data. The individual chapters cover the following areas:actinide elements (other than for reuse as nuclear fuel or transmutation targets);group 1 and 2 metals;noble gases;platinum group metals;rare earth elements; zirconium (the cladding used in most nuclear fuels); andthe industrial and medical applications of radioisotopes and the recycling of hardware. In general, each chapter summarises the opportunities and motivations for recovering the specific components as well as exemplar separation processes designed to recover them. The report’s key conclusions are that:The recycling of actinides for use other than as a nuclear fuel or transmutation targets is limited. The main emerging interest lies in applications for actinides as radioisotope power sources for spacecraft, i.e. 238Pu and 241Am.Methods for extracting the high-heat generating isotopes of caesium and strontium from high-level waste have been developed. These isotopes can primarily be decayed in storage ,but applications also exist – notably the use of 137Cs in vitrified pencils for blood irradiation in India. 90Sr has applications in nuclear medicine and power sources.136Xe has significant potential commercial value for various applications, including in the semiconductor industry and for lighting, space and medical uses. Platinum group metals have high values. However, the strategy to recover these materials needs to include periods of decay storage to allow them to meet the free release threshold.Spent nuclear fuel is also a rich source of rare earth elements, and minor actinide separation processes may be viable ways of recovering these elements during advanced reprocessing. Zirconium represents about 25% of the mass of spent nuclear fuel. Although the zircaloy has significant value, 93Zr produced by neutron activation renders the recovered zirconium mildly radioactive. Processes for zirconium removal and recovery have been proposed based on conversion to volatile zirconium tetrachloride but the economics of this are not clear. Options also exist for mechanically separating other hardware components, enabling the reuse of materials in nuclear waste management, for example.Opportunities for recovering various isotopes from spent nuclear fuels for other industrial and medical applications exist but are subject to limitations due to their use outside the nuclear fuel cycle.While the justification for reprocessing and recycling spent fuels is typically based on the economic and environmental advantages of reusing special nuclear materials (uranium, plutonium) and reducing radioactive waste for disposal (by the transmutation of minor actinides or decay storage of high-heat generating radionuclides), it can be seen that using materials from residual waste provides similar benefits as well. This report thus provides a timely and up-to-date summary of the opportunities for recycling materials from spent nuclear fuels for other applications that will be relevant to those interested in both the technical and strategic directions of nuclear energy and its fuel cycle.The key conclusion of the report is that the analysis of future nuclear fuel cycles should include studies of the valorisation of spent fuel considering all possible applications of the materials it contains, not just the recycling of uranium and plutonium for nuclear fuels, and must account for changing socioeconomic factors and the drive towards sustainability.1. Introduction1.1. Context Public acceptance is recognised as a key challenge for the nuclear sector. The benefits of nuclear technology, such as the ability of nuclear power plants to generate massive amounts of electricity with low carbon emissions, as well as the use of nuclear medicine to diagnose and treat many illnesses, are widely recognised. However, there are concerns about the use of nuclear energy due to the sector’s historic connection to nuclear weapons programmes, nuclear accidents (e.g. Three Mile Island, Chernobyl, Fukushima Daiichi) and the legacy of nuclear waste, among other things. Therefore, addressing public concerns related to the management of nuclear waste is one of the key issues that can have significant impact on the public acceptance of nuclear energy (NEA, 2010a).Nuclear energy generates irradiated (used or “spent”) nuclear fuels that are highly radioactive and must be safely and securely managed in the short term (interim storage period) and in the long term by isolating them from people and the environment. Two basic options exist for the management of spent nuclear fuels (SNFs) – direct disposal in a deep geological repository (DGR) or recovery of the valuable materials for reuse with a smaller residue of radioactive waste sent to a DGR. These are respectively known as open and closed nuclear fuel cycles (WNA, 2021). The open fuel cycle is the simplest technological option, although no DGR for SNF disposal yet exists; Finland and Sweden have the most advanced programmes, with DGRs likely to be operating in the late 2020s to early 2030s (Kadak, 2021). In the open (or once-through) fuel cycle, SNFs are stored (underwater in ponds or in dry stores) for several decades before being encapsulated in canisters for direct disposal underground in a DGR. Since no radioactive materials are separated from the SNF, the open cycle generates the maximum amount of high-level (that is, heat generating) radioactive waste, which requires the largest amount of space in a DGR and takes the longest time for the radioactivity to decay to background levels. The open cycle also uses the most natural uranium resources, which must be mined, enriched and fabricated into new fuel to be only used for a single pass through a reactor. However, in addition to its technological simplicity, the open cycle avoids any separation of nuclear materials like plutonium, minimising the risk of the diversion of such materials in the back end of the fuel cycle. After sufficient decay time (a century or more), a DGR could also be considered a mine for uranium and plutonium and, as will be shown later in this report, other valuable materials.There are variations on the closed fuel cycle, depending on the desired degree of materials recycling. Materials that can be recycled include (Croff et al., 2007; Andrews, 2008):uranium and plutonium for reuse in mixed oxide (MOX) fuels – this is usually known as MOX recycling or the twice through cycle (TTC) or mono-recycling;uranium and plutonium recycled multiple times, usually in fast reactors, although this can also be achieved in thermal reactors – this is usually known as multi-recycling;minor actinides recycled for burning in advanced reactors or waste transmuters – this is usually referred to in the partitioning and transmutation scenario (P&T);long-lived fission products (LLFP) for transmutation and/or heat-generating fission products (FP) for decay storage;other materials, elements or isotopes for uses other than nuclear fuels or transmutation targets, including applications outside the nuclear fuel cycle.While nuclear energy should, per se, be considered a sustainable energy source due to its low-carbon credentials, closed fuel cycles are generally considered to be more “sustainable” than the open cycle because they extend the use of natural resources, reduce the environmental footprint of nuclear energy by reducing the need for uranium mining, and reduce the burden of the radioactive waste on a DGR. The reduction in the waste burden can be considered a combination of the degree of recycling carried out to avoid material being classified as waste and of the reduction in volume of high-level waste generated, both of which will reduce the size of a DGR. Another consideration is the “lifetime” of the waste as measured by its radiotoxicity; the removal or separation of toxic species may permit the waste to be characterised and treated as lower activity waste and/or concentrates higher activity material in smaller volumes (Poinssot et al., 2015). However, closing the fuel cycle requires additional back-end fuel cycle facilities: first, a reprocessing plant to separate and recover the target elements and, second, a fuel fabrication plant capable of handling the reprocessed products as well as associated plants for managing the residual (or secondary) waste and interim storage facilities. Reactors must be available that have the capabilities to use the recycled product fuels. Meanwhile, the need to reprocess the SNF and to recycle nuclear materials (primarily plutonium) between facilities raises concerns over the potential diversion of nuclear materials and the perceived risks of nuclear proliferation (Cheng and Bari, 2021). Economics is another key factor that influences the choice of nuclear fuel cycle (Taylor et al., 2022). Closed cycles require more facilities compared to the open cycle but the size (and hence cost) of a DGR is smaller and the front-end fuel cycle activities are reduced. Therefore, it is not a simple exercise to estimate the costs of different fuel cycle options. Most studies that consider the levelised cost of electricity show little difference between open and closed cycles since the costs are dominated by the reactors rather than the front- or back-end fuel cycles (De Roo and Parsons, 2011). Closed cycles require nearer-term capital investment in reprocessing and fuel fabrication plants compared to the open cycle whereas spent fuel management costs can be deferred by long periods of interim storage. Also, while closed cycles offer better utilisation of uranium, the uranium “break-even” price (i.e. the level at which the price of uranium needs to be for the closed cycle to become economically attractive) is generally found to be much higher than recent trends in uranium prices (Bunn et al., 2003). Uranium prices have been rising since 2020 and mineral reserves decreasing. Geopolitical dislocations in this period have also been favouring sustainable cycles for some countries (NEA, 2023).Many countries are choosing the open cycle due to its simplicity, with no separation of nuclear materials needed, and its short-term economic advantages (IAEA, 2022). Trends may yet change over the next decades as closed cycles are more aligned with the concept of the “circular economy” and sustainability by recycling useful materials, reducing waste for disposal (and the impacts of a DGR on communities) and reducing the environmental footprint of nuclear energy (Poinssot et al., 2014). As noted above, in addition to nuclear materials for reuse as fuels or transmutation targets in the nuclear fuel cycle, which is of course the primary motivation for reprocessing spent fuel and recycling actinides, other materials could be recycled from SNF for applications outside the fuel cycle and/or to further reduce the waste for disposal in a DGR. Some of these may not be economically attractive per se but provide additional societal benefits. Closed cycles may in this way increase the public acceptability of nuclear energy as a low-carbon energy source. To develop sustainable advanced closed fuel cycles, however, requires research and development of both improved and advanced nuclear technologies, including options for processing and recycling materials other than uranium and plutonium for nuclear fuel production (Collins et al., 2010). 1.2. MotivationIn the management of SNF, the greatest benefit of recycling is the ability to close the nuclear fuel cycle, whereby the products from fuel reprocessing are recycled to produce further nuclear fuel. There is a need to demonstrate that the future, advanced recycle flowsheets and innovative technologies meet the challenge of reducing costs, proliferation risks and environmental impacts of SNF reprocessing. Therefore, any future advanced recycle regime for SNF will not only need to demonstrate technical and efficiency improvements over historical reprocessing but will also need to demonstrate that it minimises environmental impacts and reduces the overall environmental footprint of nuclear energy. This may include reducing as far as possible the waste volumes, heat load and radiotoxicity for disposal and potentially the recovery of materials that can be reused within the process or recycled for other uses, either for nuclear or non-nuclear applications. Thee recycling of nuclear materials for fuels and the reduction of waste for disposal has already been extensively studied; therefore, this review is primarily focused on the latter aspect and seeks to review the state of the art regarding the recovery of materials of value from the recycle waste streams other than uranium, plutonium and minor actinides for nuclear fuel manufacturing.While the recovery of non-actinide materials from spent fuels has been considered since the earliest days of the nuclear sector, the economics and technical feasibility change with time, either due to advances in technology or changing societal attitudes. As the global focus on sustainable development and the circular economy has increased, it is timely to review the potential benefits and options for recycling “other” materials from SNF. Geopolitical shifts have also increased focus on the security of supply of energy and critical materials; this too favours recycling in closed fuel cycles.1.3. ScopeThis report reviews the opportunities for recovering various elements and/or isotopes from SNF for applications other than use in new nuclear fuels or transmutation targets, which are addressed in a wide variety of NEA publications (NEA 2010b; NEA, 2018; NEA, 2021), and elsewhere (EASAC, 2014; Taylor, 2015; Wigeland et al., 2014). The focus therefore is mainly on non-actinide elements, including platinum group metals and rare earths, radioisotopes such as 137Cs and 90Sr and structural materials (zirconium). Some specific actinide separations that lead to alternative applications, including the recovery of neptunium for 238Pu production for space power are addressed. The motivation, benefits, difficulties and means of recovering these materials is also examined.1.4. ReferencesAndrews, A. (2008), Nuclear Fuel Reprocessing: US Policy Development, CRS Report for Congress, Order Code RS22542, https://apps.dtic.mil/sti/citations/ADA458841.Bunn, M., S. Fetter, J.P. Holdren and B. van der Zwaan (2003), The Economics of Reprocessing vs. Direct Disposal of Spent Fuel, Final Report for Project on Managing the Atom, DE-FG26-99FT4028, Belfer Center for Science and International Affairs, Harvard University, United States.Cheng, L.Y. and R.A. Bari (2021), “Non-proliferation aspects of nuclear energy”, Encyclopedia of Nuclear Energy, edited by E Greenspan, Elsevier, pp. 733-743, https://doi.org/10.1016/B978-0-12-819725-7.00120-3.Collins, E.D., G.D. Del Cul, J.E. Rushton and K.A. Williams (2010), A Practical Solution to Used Nuclear Fuel Treatment to Enable Sustained Nuclear Energy and Recovery of Vital Materials, ORNL/TM-2010/81, Oak Ridge, Oak Ridge National Laboratory, United States.Croff, A., R.G. Wymer, L.L. Tavlarides, J.H. Flack and H.G. Larson (2007), Background, Status, and Issues related to the Regulation of Advanced Spent Nuclear Fuel Recycle Facilities, US Nuclear Regulatory Commission, United States, www.nrc.gov/reading-rm/doc-collections/nuregs/staff/sr1909/index.html.De Roo, G. and J. Parsons (2011), “A methodology for calculating the levelized cost of electricity in nuclear power systems with fuel recycling”, Energy Economics, Vol. 33, pp. 826-839, https://doi.org/10.1016/j.eneco.2011.01.008.EASAC (2014), Management of Spent Nuclear Fuel and its Waste, EASAC, JRC Reference Report, Belgium.IAEA (2022), Status and Trends in Spent Fuel and Radioactive Waste Management, International Atomic Energy Agency, Austria, www.iaea.org/publications/14739.Kadak, A.C. (2021), “Nuclear waste can be disposed of safely”, Encyclopaedia of Nuclear Energy, edited by E Greenspan, pp. 760-774, Elsevier. NEA (2023), Uranium 2022: Resources, Production and Demand, OECD Publishing, Paris, www.oecd-nea.org/jcms/pl_79960.NEA (2021), Strategies and Considerations for the Back End of the Fuel Cycle, OECD Publishing, Paris, www.oecd-nea.org/jcms/pl_55928. NEA (2018), State-of-the-art Report on the Progress of Nuclear Fuel Cycle Chemistry, OECD Publishing, Paris, www.oecd-nea.org/jcms/pl_14970. NEA (2010a), Public Attitudes to Nuclear Power, OECD Publishing, Paris, www.oecd-nea.org/jcms/pl_14534. NEA (2010b), National Programmes in Chemical Partitioning: A Status Report, OECD Publishing, Paris, www.oecd.org/publications/national-programmes-in-chemical-partitioning-9789264106871-en.htm.Poinssot, C. et al. (2014), “Assessment of the environmental footprint of nuclear energy systems: Comparison between closed and open fuel cycles”, Energy, Vol. 69, pp. 199-211, https://doi.org/10.1016/j.energy.2014.02.069.Poinssot, C., B. Boullis and S. Bourg (2015), “Chapter 2: Role of recycling in advanced nuclear fuel cycles”, Reprocessing and Recycling of Spent Nuclear Fuel, pp. 27-48, Woodhead Publishing, Oxford, https://doi.org/10.1016/C2013-0-16483-5.Taylor, R. (2015), Reprocessing and Recycling of Spent Nuclear Fuel, 1st edition ed., p. 660, Woodhead Publishing, Oxford, https://doi.org/10.1016/C2013-0-16483-5. Taylor, R., W. Bodel and G. Butler (2022), “A Review of environmental and economic implications of closing the nuclear fuel cycle, Part Two: Economic impacts”, Energies, Vol. 2472, https://doi.org/10.3390/en15072472.Wigeland, R. et al. (2014), Nuclear Fuel Cycle Evaluation and Screening, Final Report, FCRD-FCO-2014-000106, pp. 1-51, INL/EXT-14-31465 Fuel Cycle Research and Development, United States Department of Energy, Idaho National Laboratory, United States.WNA (2021), “Nuclear fuel cycle”, www.world-nuclear.org/information-library/nuclear-fuel-cycle.aspx (accessed 31 January 2022).2. Background2.1. Spent fuel characteristicsThere are multiple types of nuclear fuel that have been used or studied historically (NEA, 2018), such as metallic uranium, oxide, nitride, carbide systems or metal alloys, inert matrix fuels, high-temperature reactor (coated particle) fuels and molten salt for molten salt reactors (MSRs). However, the main ones used internationally are:thermal uranium oxide – the standard fuel from thermal reactors, with increasing burn-up;thermal (U, Pu) mixed oxide fuel – up to 10% plutonium content.This report focuses on oxide fuel types because these are the most common in use.Since about 2020, there has been a rising interest in high assay low-enriched uranium (HALEU) fuels, which are defined as uranium-based fuels with an enrichment higher than 5% but lower than 20%, which is the limit for non-weapons usable materials. The residual enrichment from HALEU could range from 5% to 13%, making recycling and reuse more economically attractive.2.1.1. Typical characteristics and reusable components in spent nuclear fuel (SNF)Most of the 500 commercial nuclear energy reactors operating or under construction in the world today are light water reactors (of two types – pressurised water reactor [PWR] and boiling water reactor [BWR]). Fuel for these reactors is uranium, generally enriched to 3-5 w% 235U with the remainder being 238U (WNA, 2020a). The chemical form of the uranium is uranium dioxide (UO2) pellets, a ceramic-like material that is encased in zircaloy tubing to form fuel pins. A number of these fuel pins are combined into fuel assemblies, held together with stainless steel and Inconel spacer grids. Heavy stainless-steel nozzles are affixed to each end of the fuel assembly to facilitate handling, placement in the reactor and insertion of control rods at the top of the assembly. For example, a Westinghouse PWR fuel assembly has a 17 × 17 pin array, of which 264 array positions are occupied by fuel pins, and the remaining positions are used for control rods. A common PWR fuel assembly contains ~525 kg of UO2 (~461 kg U metal), ~108 kg of zircaloy, and ~26 kg of other steel-based hardware (Croff and Alexander, 1980). Details on various types of fuels assemblies can be found elsewhere (US DOE, 1992).Nuclear fission of 235U produces heat, neutrons and fission products (FPs). Some of the neutrons can transmute the uranium, especially the 238U, to transuranium (TRU) elements, such as 239Pu, that build up over time and participate in the fission process. As the fissile content is consumed and the FPs build up, the fuel elements must be removed from the reactor and replaced, usually after 3-5 years. The composition of the fuel at that point will vary depending on the initial enrichment and how long it was in the reactor, but typically contains approximately (WNA, 2020b):95.6% uranium, over 98.5% of which is 238U (the remainder being: trace amounts of 232U and 233U; <0.02% 234U; 0.5-1.0% 235U; ~0.5% 236U; and ~0.001% 237U);2.9% stable fission products;0.9% plutonium;0.3% caesium and strontium (fission products);0.1% iodine and technetium (fission products);0.1% other long-lived fission products;0.1% minor actinides (americium, curium, neptunium).As an example, Figure 2.1 shows the average weight composition of the spent nuclear fuel produced in commercial reactors in the United States from 1968 to 2002 and calculated on the basis of 40 years of cooling (Del Cul et al., 2007).Figure 2.1. Average weight composition, PWR and BWR fuel, accumulated from 1968 to 2002Source: NEA EGFRW data, 2022.Reprocessing as practised in, for example, France, the United Kingdom and Russia recovers separated pure uranium and plutonium products from the SNF. Recycling of plutonium and uranium into new fuel has been less efficient, with some countries acquiring stockpiles of nuclear materials although France, for instance, promptly recycles its reprocessed plutonium as MOX fuel for thermal reactors. This twice-through cycle using MOX fuel is the only spent fuel management solution deployed at the commercial scale and thus is a proven technology. Clearly, in the future energy market it will be essential that nuclear energy be cost-competitive, but equally important will be the ability to demonstrate that it is environmentally sustainable. Life cycle analysis techniques have shown that nuclear energy, even with the open cycle, is comparable in environmental impact performance to renewable electrical generation (World Energy Council, 2004; Odeh et al., 2013), although the relative performance of the different electricity generation methods depends greatly on assumptions made about locations and materials used in construction and operation. In the case of nuclear energy, the dominating issue is the uranium supply since the method of mining, the grade of ore and enrichment method are the greatest source of greenhouse gas emissions, amounting to about 38% of total greenhouse gas emissions (Poinssot et al., 2014). In view of this, it is not surprising that minimising the mining of natural uranium by utilising spent fuel recycling greatly improves the environmental performance and reduces the volume of waste for disposal and the radiological impact (Poinssot et al., 2015; Paulillo et al., 2020). Looking to the future, roadmaps for the development of the nuclear fuel cycle typically involve multiple recycling in advanced reactors, which will further promote the long-term sustainability of nuclear systems; this is exemplified by the roadmap adapted from Poinssot et al. (2015) illustrated in Figure 2.2. Figure 2.2. Suggested roadmap of anticipated future fuel cycle to promote the sustainability of nuclear energy systemsSource: Based on Poinssot, Boullis and Bourg, 2015.The suggested approach involves operating increasingly efficient extraction processes to partition uranium and plutonium from the ultimate waste, which comprises mainly fission products and minor actinides. The ambition should be to reach multiple recycling beyond the “twice-through cycle” (TTC) and eventually look to recycle the minor actinides to minimise the waste in a DGR. It should be noted that this report does not specifically consider the reuse of materials from thorium-based SNF. Thorium energy and fuel cycles are not implemented industrially although they have been researched for several decades. For example, the reprocessing of thorium fuel has been demonstrated at pilot scale, notably in the United States to reprocess about 900 tonnes of thorium fuel (~1.5 tonnes 233U) and in France. This utilised the thorium extraction (THOREX) liquid-liquid extraction process, which is like the plutonium uranium reduction extraction (PUREX) process, but the THOREX process has yet to reach the maturity of the commercial PUREX process. The key issues are (NEA, 2015):To take the THOREX process to full industrial scale requires further development of the dissolution, liquid-liquid extraction and conversion steps. The dissolution of thorium metal or oxide is more complex than for uranium and requires the addition of hydrofluoric acid, whose corrosiveness must be buffered by adding aluminium nitrate to protect process equipment.The low solubility of the Th-TBP complex and the interaction between the main tributyl phosphate (TBP) degradation product, dibutyl phosphate and thorium create difficulties in the purification step by liquid-liquid extraction. These problems may be overcome by modifying the solvent formulation, e.g. by replacing TBP or the diluent. Currently, no developed alternative to variants of the THOREX exists for reprocessing thorium-based fuels although other extractants have been investigated.The influence of the burn-up and the impact of the conversion and fabrication process and fuel microstructure require further investigation.Additionally, a major challenge associated with thorium reprocessing is related to the unavoidable presence of 232U, which accompanies 233U. One of its decay products, 208Tl, is a 2.6 MeV gamma emitter that will require substantial changes in the downstream fuel fabrication process because it cannot be handled in gloveboxes, as is the case for (U,Pu)O2 MOX fuel. Thus, a remotely operated and a fully shielded facility is required for the entire recycle fuel fabrication process. The uranium-thorium fuel cycle can also be utilised in MSRs as originally demonstrated at the Oak Ridge National Laboratory (ORNL) (Dolan, 2017; Uhlíř, 2007). 2.1.2. The waste hierarchyA fully sustainable system would embrace environmental best practices and apply the principles of the waste hierarchy (see Figure 2.3), which gives top priority to preventing waste in the first place. When waste is created, it gives priority to preparing it for reuse, then recycling, then recovery and, last of all, disposal (Turner et al., 2021). The waste hierarchy is similar to the circular economy in that the intention is to repurpose, reuse or recycle materials in the economy as far as possible to minimise the use of natural resources and the waste generated by economic activities. It has the advantage of being more widely applied in the nuclear sector during the development and authorisation of waste management strategies. The following sections will discuss the materials that could be recovered and made available for other uses.Figure 2.3. Illustration of the waste hierarchySource: NEA EGFRW data, 2023.2.2. Potentially recoverable materials Based on the composition of spent fuel shown in Figure 2.1 and applying the principles of the waste hierarchy, it is proposed by Stéphane Bourg and Christophe Poinssot (Bourg and Poinssot, 2017) that potentially about 99% by weight of the spent nuclear fuel components could be recovered for reuse or recycled. The main groups are listed in Table 2.1 below:Table 2.1. Recoverable components in spent nuclear fuelComponentFraction (w%)Uranium66.4Zirconium (from cladding)24.6Hardware (nozzles, end pieces, supports etc. made of steel, Inconel.)5.4Transuranics (Pu, Am, Np & Cm)0.7Light lanthanides (La, Ce, Pr, Nd)0.7Noble gases (Xe, Kr)0.4Noble metals (Ru, Rh, Pd, Ag)0.3Figure 2.4. Mass of nuclides against atomic mass for 10 years cooled, 50 GWd/tHM burn-up MOX fuelSource: NEA EGFRW data, 2022.Studies and recent developmental efforts have shown that it is possible to recover components other than uranium and plutonium, such as the zirconium in cladding (Collins et al., 2017; Del Cul et al., 2014). Examining the composition of SNF in more detail (by using outputs from fuel inventory codes such as FISPIN), it possible to plot the mass of each radionuclide present against the atomic mass, as shown in Figure 2.4. This figure shows two distinct groups of nuclides present at masses greater than 10 g/tHM either side of atomic mass 120, the first corresponding to atomic mass ~85 to 110 and the second at atomic mass ~130 to 155. Not surprisingly, similar results are shown with other fuels at different burn-ups; for example, a study from the French Alternative Energies and Atomic Energy Commission (CEA) (Bourg and Poinssot, 2017) looked at a representative uranium oxide (UOX) spent fuel that had a burn-up of 47.5 GWd/t and was 10year cooled. That study highlighted that the groupings in the middle of the plot align with the platinum group and other noble metals and the rare earth elements respectively. Since these elements are of high value and scarce, it is reasonable to assume that the recycling of spent fuel presents an opportunity to recover these and other scarce materials. The significant feature of the data in Figure 2.4 is that the FP peaks align with nuclides present in amounts approaching or exceeding kilogram quantities, i.e. amounts that are likely to make recovery viable. For example, 139La, 140Ce and 141Pr are present at approximately 1.5 to 1.6 kg/tHM; 101Ru, 102Ru and 104Ru are each present at about 1.2 to 1.4 kg/tHM and both 105Pd and 106Pd at approximately 1.0 kg/tHM. An arbitrary threshold mass of 10 g/tHM is suggested as an amount that may need to be present in SNF for recovery to be viable and this level is indicated in Figure 2.4.However, merely looking at the mass of nuclides present ignores the major issue of the differing levels of radioactivity associated with each of the nuclides. For example, while 105Pd and 106Pd are stable, approximately 17.8% of the total palladium in spent fuel will be 107Pd – a beta emitter with a half-life of 6.5 million years. The presence of 107Pd prevents the palladium from being recovered as a free-release material.Consequently, even though stable isotopes of elements of interest are present in significant quantities, the presence of unstable isotopes (even significantly lower quantities) can be sufficient to make the desired material too active for recovery to be practical or viable. That issue, along with the means of recovery and the technical and commercial drivers for recovery to be attempted, will be discussed in the following sections.2.3. Demand for materialsAs highlighted earlier, due to the wide range of elements present in SNF recycle waste streams, it is not surprising that many of them may be of interest for use in other processes related to nuclear energy or in general industrial applications, especially when those elements are in high demand and not abundantly available in nature. The strategic importance of these materials has been highlighted in several reviews and studies undertaken by governments and international bodies.2.3.1. US review in 2018 of critical mineralsIn response to US Presidential Executive Order 13817 (Executive Office of the President, 2017), the US Secretary of the Interior published the draft list of critical minerals (83 FR 7065) (Department of the Interior, 2018) in the Federal Register. Critical materials were defined as being: …a non-fuel mineral or mineral material essential to the economic and national security of the United States, the supply chain of which is vulnerable to disruption, and that serves an essential function in the manufacturing of a product, the absence of which would have significant consequences for our economy or our national security. The draft list consisted of 35 minerals or mineral material groups, as follows:Aluminium (bauxite), antimony, arsenic, barite, beryllium, bismuth, caesium, chromium, cobalt, fluorspar, gallium, germanium, natural graphite, hafnium, helium, indium, lithium, magnesium, manganese, niobium, platinum group metals (PGM), potash, the rare earth elements (REE) group, rhenium, rubidium, scandium, strontium, tantalum, tellurium, tin, titanium, tungsten, uranium, vanadium, and zirconium.2.3.2. European Union review of critical raw materialsSimilarly to the United States, the European Union has undertaken a review (European Commission, 2014) of the supply of raw materials and identified 20 that are deemed critical. They are antimony, beryllium, borates, chromium, cobalt, coking coal, fluorspar, gallium, germanium, graphite (natural), indium, magnesite, magnesium, niobium, platinum group metals, phosphate rock, the rare earth elements (both heavy and light), silicon, tungsten.The EU review distinguishes between the different rare earth elements as shown below in Table 2.2.Table 2.2. EU categorisation of rare earth elementsGroup CategoryRare earth elements includedRare earth elementsScandiumScandiumRare earth elements – lightLanthanum, cerium, praseodymium, neodymium, samariumRare earth elements – heavyEuropium, gadolinium, terbium, dysprosium, erbium, yttriumOthers (holmium, thulium, ytterbium, and lutetium)Significantly, the EU review shows that the major producers of these raw materials are located outside the European Union, with the People’s Republic of China being the most influential and others such as the United States (for beryllium) and Brazil (for niobium) being dominant for specific materials. This implies that, beyond the technical challenges related to the extraction and transportation of the materials, there is an additional risk stemming from geopolitical factors.Noting a risk of a future market deficit for critical materials such as antimony, indium, platinum group metals and the heavy rare earths, the review recommended to the European Union:To initiate all the necessary specific actions to ensure undistorted and reliable access to critical raw materials given the combination of their economic importance and supply risk, as well as for non-critical raw materials where appropriate.However, it did not detail the actions to be taken.2.4. Critical materials to target for recovery from recycling SNFAs highlighted in the previous sections, the prevalence of the platinum group metals and the rare earth elements in spent nuclear fuel, along with their identification as critical materials, makes those materials prime targets for recovery from streams during nuclear fuel recycling. Those materials were also identified by Stéphane Bourg and Christophe Poinssot (Bourg and Poinssot, 2017) who compared the amounts of critical elements available in spent fuel with the total world production of those elements. So, for example, they calculated that based on 2014 data, the potential annual production of ruthenium from French nuclear fuel may be as high as 21.79% of world production. For rhodium that figure would be 3.51% and for samarium 0.18%. However, cerium and gadolinium were only 0.01 and 0.02%, respectively.In their analysis, Bourg and Poinssot selected 0.1% of total world production as an arbitrary trigger value for which recovery from French spent nuclear fuel may in theory be viable (simply based on possible capacity and with no regard to possible technical difficulties and efficiency). This is a reasonable starting point in identifying the materials to target for recovery, but there may be other factors to consider, such as the possible ability to recover material in higher purity without the presence of other elements that often occur concurrently with the target element in naturally occurring mineral ores. Additionally, it should be noted that some potentially recoverable radioactive materials are needed for radiological purposes. Consequently, the following sections discuss the recovery of elemental materials from reprocessing waste streams and their potential for reuse in both nuclear and non-nuclear applications. In addition, the potential recovery and reuse of individual radioisotopes is highlighted.2.5. ReferencesBourg, S. and C. Poinssot (2017), “Could spent fuel be considered as a non-conventional mine of critical raw materials?”, Progress in Nuclear Energy, Vol. 94, pp. 222-228, https://doi.org/10.1016/j.pnucene.2016.08.004.Collins, E.D. et al. (2017), “Engineering scale development/demonstration of zirconium recovery from used fuel cladding”, ANS Annual Meeting, San Francisco, California, 11-15 June.Croff, A.G. and C.W. Alexander (1980), Decay Characteristics of Once-through LWR and LMFBR Spent Fuels, High-level Waste, and Fuel-assembly Structural Material Waste, ORNL/TM-7431, Oak Ridge National Laboratory, Oak Ridge, TN: Oak Ridge National Laboratory, United States.Del Cul, G.D., B.B. Spencer and E.D. Collins (2007), “A new paradigm: Near-complete recycling of spent fuel – a path to sustainable nuclear energy”, Proceedings of Global 2007 International Conference, Advanced Nuclear Fuel Cycles and Systems, Boise, Idaho.Del Cul, G.D., E.D. Collins, B.B. Spencer and R.D. Hunt (2014), “Recovery, purification, and recycle of zirconium from used nuclear fuel”, NM: Actinide Separations Conference, Albuquerque, New Mexico.Department of the Interior (2018), “Federal Register, Draft List of Critical Minerals, 83 FR 7065”, www.federalregister.gov/documents/2018/02/16/2018-03219/draft-list-of-critical-minerals. (accessed in November 2023).Dolan, T.J. (2017), Molten Salt Reactors and Thorium Energy, 1st edition ed., Woodhead Publishing, Elsevier, Duxford, pp. 1-815, United Kingdom.European Commission (2014), Report on Critical Raw Materials for the EU, Ares (2015)1819503 – 29/04/2015, https://rmis.jrc.ec.europa.eu/uploads/crm-report-on-critical-raw-materials_en.pdf (accessed in November 2023).Executive Office of the President (2017), “US Presidential Executive Order 13817 of December 20, 2017” www.federalregister.gov/documents/2017/12/26/2017-27899/a-federal-strategy-to-ensure-secure-and-reliable-supplies-of-critical-minerals (accessed in November 2023).NEA (2018), State-of-the-art Report on the Progress of Nuclear Fuel Cycle Chemistry, OECD Publishing, Paris, www.oecd-nea.org/jcms/pl_14970. NEA (2015), Introduction of Thorium in the Nuclear Fuel Cycle: Short- to long-term considerations, OECD Publishing, Paris, www.oecd-nea.org/jcms/pl_14930. Odeh, N., N. Hill and D. Forster (2013), Current and Future Lifecycle Emissions of Key ‘Low Carbon’ Technologies and Alternatives, Ricardo-AEA (Reference: ED58386), Report for the Committee on Climate Change, Harwell, United Kingdom. Paulillo, A., J. M. Dodds, A. Milliken, S. Palethorpe and P. Lettieri (2020), “The environmental impacts of reprocessing used nuclear fuels: A UK case study”, Sustainable Materials and Technologies, Vol. 25, https://doi.org/10.1016/j.susmat.2020.e00186.Poinssot, C., S. Bourg, N. Ouvrier, N. Combernoux, C. Rostaing, M. Vargas-Gonzalez and J. Bruno (2014), “Assessment of the environmental footprint of nuclear energy systems. Comparison between closed and open fuel cycles”, Energy, Vol. 69, pp. 199-211, https://doi.org/10.1016/j.energy.2014.02.069. Poinssot, C., B. Boullis and S. Bourg (2015), “Chapter 2: Role of recycling in advanced nuclear fuel cycles”, Reprocessing and Recycling of Spent Nuclear Fuel, pp. 27-48, Woodhead Publishing, Oxford, https://doi.org/10.1016/C2013-0-16483-5.Turner, J., J. Spencer, L. O’Brien, S. Palethorpe, A. Banford and R. Taylor (2021), “Applying the waste hierarchy for future recycling of nuclear fuels”, Nuclear Future, Vol. 17 (6), pp. 43-50.Uhlíř, J. (2007), “Chemistry and technology of molten salt reactors – history and perspectives”, Journal of Nuclear Materials, Vol. 360, Issue 1, pp. 6-11, https://doi.org/10.1016/j.jnucmat.2006.08.008. US DOE (1992), Characteristics of Potential Repository Wastes, DOE/RW-184-R1-V1, Washington, DC, Office of Civilian Radioactive Waste Management, United States.World Energy Council (2004), Comparison of Energy Systems Using Life Cycle Assessment, World Energy Council, London, www.worldenergy.org/publications/entry/comparison-of-energy-systems-using-life-cycle-assessment.WNA (2020a), Uranium enrichment, www.world-nuclear.org/information-library/nuclear-fuel-cycle/conversion-enrichment-and-fabrication/uranium-enrichment.aspx (Accessed September 2021).WNA (2020b), Processing of used nuclear fuel, www.world-nuclear.org/information-library/nuclear-fuel-cycle/fuel-recycling/processing-of-used-nuclear-fuel.aspx (Accessed December 2020).3. ActinidesAs noted previously, the recovery of actinides for nuclear fuels or transmutation targets is outside the scope of this report. Many other publications deal with the issues around the recycling of these nuclear materials; for example, see: EASAC, 2014; NEA, 2010; NEA, 2012; NEA, 2018; Baron et al., 2019; Taylor, 2015; NEA, 2021; Wigeland et al., 2014; Geist et al., 2020; Netter, 2012.This chapter focuses on other applications of transuranic actinides that could be recovered from spent fuels.3.1. NeptuniumNeutron capture on 238U and 235U leads to the production of 237Np and subsequent generation of 238Pu. 237Np is produced by neutron capture and beta decay of both 238U and 235U via the following reactions (Schulz and Benedict, 1972):238U(n,2n) →237U(β t½=6.7d) → 237Np;235U(n,γ) →236U(n,γ) →237U(β t½=6.7d) → 237Np.After recovery and purification of the 237Np, it can be converted to 238Pu via the following reaction:237Np (n, γ) → 238Np (β t½=2.1d) → 238Pu.The primary use for 238Pu is as the heat source in radioisotope thermoelectric generators (RTGs). The selection of 238Pu for this purpose is its 88-year half-life, giving a high specific activity leading to radiogenic heating (power density of 0.567 W/g – see Table 3.1). Multi-kilogram amounts are needed to power the instrument packages on deep space missions, and smaller amounts are needed for medical needs, such as in heart pacemakers, and for research. A case study is described below.3.1.1. Reuse of 237Np for production of 238Pu in the United StatesIn the United States, the need for 238Pu has been met through the operation of government-owned plutonium production reactors. From the early 1960s to the early 1990s, the 238Pu was produced and recovered in several tens of kilogram amounts per year at the Savannah River Site (SRS) (Schulz and Benedict, 1972; Porter, 1964; Myrick and Folger, 1964; Burney, 1964; Groh and Schlea, 1970). Since the large-scale facilities have now closed, continuing needs are planned to be met (Wham et al., 2015) using the existing inventory of 237Np, which is irradiated and transmuted in existing research reactors at Oak Ridge National Laboratory (ORNL), using the High Flux Isotope Reactor, and at Idaho National Laboratory (INL), using the Advanced Test Reactor (ATR), with post-irradiation chemical recovery, purification and target fabrication carried out in the existing transuranium element production hot cells (King et al., 1981) of the Radiochemical Engineering Development Center (REDC) at ORNL.If future needs grow, the 237Np required likely will need to be met by new neptunium recovered from power-reactor spent fuel.Based on reactor physics modelling calculations, in a typical pressurised water reactor, fuelled with low-enriched uranium (4.7% 235U), the yield of 237Np is 570 g/tHU after 45 GWd/t burn-up, and 777 g/tU after 60 GWd/t burn-up. There are several important side reaction constraints that must be considered in the overall path for production of 238Pu from 237Np as illustrated in Figure 3.1.Figure 3.1. Transmutation path for production of 238Pu from 237NpSource: NEA EGFRW data, 2023.First, considering that the neutron capture cross-section of 238Pu is about three times greater than that of 237Np, the extent of the transmutation irradiation must be limited to convert only 10 to 15% of the 237Np to minimise the production of 239Pu and heavier isotopes of plutonium and maintain the isotopic purity of the 238Pu >82% by mass, for efficient use in RTGs. Second, the (n,2n) reaction of 237Np must be minimised to prevent the formation of 236Pu and its decay daughters, which have strong gamma emission. Such excessive radiation could damage the instrument package, which on deep space probes for example must be maintained for decades.The functional production process path is illustrated in Figure 3.2. Since only 10-15% of the 237Np is converted to product 238Pu in each cycle, most of the 237Np is recycled and is the dominant elemental mass in the separations process. After irradiation, the targets are dissolved and chemically processed to (1) separate, purify, and convert the 238Pu to heat source oxide; (2) separate, purify, and convert the remaining (85-90%) of 237Np to NpO2 for recycle target fabrication; and (3) dispose of the fission product waste. The process steps for conversion of the recycled 237Np to NpO2 and fabrication of targets are carried out typically in unshielded gloveboxes. Therefore, prior to these steps, the 237Np must be treated to remove its decay daughter, 233Pa, which has a 0.3 KeV gamma radiation emission. Figure 3.2. 238Pu production processSource: NEA EGFRW data, 2023.There have been several approaches to the chemical processing of the irradiated materials, both to recover the 237Np from the spent fuels and then recover 238Pu from the irradiated 237Np targets, which are typically cermet aluminium and oxide matrices. At SRS, both these materials were dissolved in nitric acid containing added mercuric and fluoride ions as catalysts (Schulz and Benedict, 1972; Porter, 1964; Myrick and Folger, 1964; Burney, 1964; Groh and Schlea, 1970). The dissolver solution was then fed to the first of a three-column anion exchange process with the dissolved Al(NO3)3 and nitric acid providing the salting strength (see Figure 3.3). Control of the chemical valence of both the neptunium and the plutonium is essential to enable decontamination from fission products and partitioning from each other. Both the plutonium and neptunium products must be produced with relatively high purity because they must be subsequently handled in unshielded facilities to manufacture RTGs and recycle 237NpO2. To meet the degree of purity required, the process used at SRS utilised a strong reducing agent, ferrous sulfamate, to create Np(IV) and Pu(III) and then heating to oxidise plutonium to the extractable tetravalent state. Np(IV) and Pu(IV) were co-adsorbed by the anion resin while the aluminium and fission products were inextractable. Two cycles of co-adsorption were used to remove the fission products sufficiently from both product elements. In the second column, the co-adsorbed Pu(IV) was selectively eluted at a lower acidity than the feed solution assisted by reduction to Pu(III) by addition of ferrous sulfamate and hydrazine, thus resulting in selective removal (partitioning) of the Pu. The Np product was then stripped from the resin in slightly acidic solution and was subsequently sent to the oxalate precipitation process for conversion to oxide and recycle to target fabrication. The Pu product, containing iron and sulphur from the use of ferrous sulfamate, was reoxidised to Pu(IV) and purified in the third anion exchange column. The purified plutonium product solution was then converted to oxide powder by means of the oxalate precipitation-filtration-calcination process. The overall process is illustrated in Figure 3.3.Figure 3.3. SRS 238Pu separation processSource: NEA EGFRW data, 2023.A negative aspect of the process was that it created relatively large volumes of liquid waste, which included nitric acid, iron, sulphur, aluminium, mercury and fluorine. In addition, the used anion resins, created by frequent replacement after radiation damage rendered them no longer usable, were dissolved by wet oxidation using potassium permanganate catalyst, thus creating more liquid waste. The liquid waste was accommodated in “H-Canyon” at SRS, which contained liquid waste evaporators and access to liquid waste storage tanks. This contributed to the legacy of liquid radioactive waste at SRS.A different approach is being taken for the post-irradiation chemical processing operations at the ORNL REDC Facility (King et al., 1981). Utilisation of existing tanks, solvent extraction, ion exchange and oxide conversion equipment and processes are a driver for process selection. The overall process is illustrated in Figure 3.4.Figure 3.4. Overall ORNL chemical processing scenarioSource: NEA EGFRW data, 2023.Selective dissolution of the aluminium target matrix/cladding in caustic-nitrate solution has been the preferred method at the REDC for many years (King et al., 1981). After decantation and filtration of the aluminium-bearing caustic-nitrate solution, the residual actinide/fission product oxides are dissolved in concentrated nitric acid.Separation development work has shown that selective plutonium partitioning and decontamination by solvent extraction using tri-n-butyl phosphate (TBP) as the extractant, followed by a neptunium decontamination solvent extraction cycle works well, but requires a follow-up purification for each element by means of anion exchange to meet product specifications. Experience so far has shown that losses of both Pu and Np to the fission product waste stream are substantially lower than 0.1%.The process also includes calcination of the Pu-loaded cation exchange resin to produce a PuO2 product that is shipped to Los Alamos National Laboratory for conversion to RTG oxide pellets. The recycled neptunium is converted to NpO2 by means of the modified direct denitration process (Collins, 2015).To meet or exceed the production goal of 1.5 kg of plutonium (85% 238 Pu), multiple chemical processing campaigns, each with a duration of approximately two months, will be required each year. Therefore, the goal of the separations process development is to simplify the operations to the extent possible. Elimination or simplification of the batch anion exchange process, which is time-consuming and generates excessive waste, is a goal. Scale-up to the operational level is expected to be done before 2030.Newly generated, high-activity liquid waste management is undergoing revision at ORNL, and adequate new facilities may require multi-million-dollar funding. Obtaining funding and safety approvals, constructing new facilities and implementing operations is expected to take at least 10-20 years. Therefore, the 238Pu production project must apply an integrated approach to develop chemical processing capabilities to meet production goals while developing new waste management capabilities. An effort is under way to incorporate methods for liquid waste management into all isotope processing operations.Recovery of 237Np from irradiated uranium spent nuclear fuel in the future can enable the recovered 237Np to be used to produce 238Pu for use in radioisotope thermoelectric generators. This was done successfully in US industrial-scale facilities from the early 1960s through the early 1990s, and it is now being resumed at a smaller scale. Resumption at large scale would likely require recovery of additional 237Np from power reactor spent fuels. A recent innovative option for the 237Np/238Pu separation process has been proposed by Jarrod M. Gogolski and Mark P. Jensen (Gogolski and Jensen, 2021) to avoid contamination of the products by phosphate degradation products that are introduced by radiolysis of TBP. Various N, N-dialkylamides (decomposable extractant molecules containing only carbon, hydrogen, oxygen and nitrogen atoms) were tested for this purpose and promising results were obtained.3.2. AmericiumElement 95, americium, has two main isotopes present in spent fuels: 241Am and 243Am. This report focuses on 241Am, which has some applications outside the nuclear fuel cycle. 241Am is a radioactive daughter product from 241Pu and has a half-life of 432.8 years; it decays mainly via alpha-decay with an average alpha particle energy of 5.47 MeV into the long-lived isotope (Magill and Magill, 2010). In addition, 241Am emits soft gamma radiation at 59.94 keV and its processing requires some light shielding (2 mm Pb-equivalent) and potentially remote handling tools. Thus, protection against soft radiation from 241Am is relatively simple and useful quantities for industrial applications can be used without massive shielding. In industry, various measuring and research instruments use 241Am.The isotope 241Am is created mainly by - decay of 241Pu with a half-life of 14.33 years, and it decays into 237Np by alpha decay as stated earlier. During reactor operation, 241Pu is slowly built up in the nuclear fuel by a chain of different neutron capture reactions (n, γ) in 238U and 239Pu and subsequent radioactive decays. These processes can be described by the following equations (Runde and Schulz, 2010):Production of 239Pu: 238Un,γ239Uβ-23.5 min239Npβ-2.36 d239PuProduction of 241Pu: 239Pun,γ240Pun,γ241PuProduction of 241Am:241Puβ- 14.33 y241Amα 432.8 y237NpOver the last decades, large amounts of pure plutonium have been separated from spent fuel at the large European reprocessing plants in La Hague, France, and in Sellafield, United Kingdom (UK). Since the United Kingdom, unlike France, did not promptly refabricate the separated Pu into new MOX fuel elements, thousands of kgs of 241Am have accumulated due to the radioactive decay of the 241Pu isotope and are now part of the civil Pu stocks there (Brown et al., 2018). This americium may need to be extracted from the Pu before refabrication into fresh mixed oxide fuel if the UK plutonium is to be recycled. Furthermore, many advanced nuclear fuel cycles have proposed the partitioning and transmutation of americium from spent fuels. This is because it contributes significantly to the required gallery space and to the long-term radiotoxicity due to its relatively high isotopic power of 0.114 W/g, (Magill and Magill, 2010) and the very long half-life of its daughter isotope 237Np (2.14 million years). Therefore, it is frequently suggested that the removal of americium from the waste for transmutation in a nuclear reactor or accelerator-driven system can significantly enhance the economics, public acceptance and long-term safety of the repository (NEA, 2010; NEA, 2021; Taylor et al., 2022).Application examples include the continuous measurement of the thickness of steel and aluminium tape as well as sheet glass. Equipment with 241Am is also used to remove electrostatic charges in industry from plastics, synthetic films and paper. It is commonly used as the ionisation source inside some smoke detectors. However, like 238Pu, 241Am has also been used as a heat source for power generation within space applications. Radioisotope power systems (RPS) are based on the principle that the heat generated through high numbers of alpha decay events per second causes the material to self-heat when densified as a ceramic oxide. These heat sources can then be used within radioisotope heater units (RHUs) (Tate, 1982), used to keep instrumentation warm, or RTGs (Lange and Carroll, 2008) that generate electricity from heat through thermocouples. Since the 1960s, 238Pu has been the radioisotope of choice for RPSs and has a well-established heritage as a heat source in US space missions, with over 48 RTGs flown on 29 missions. As described above, generating 238Pu requires a significant inventory of 237Np, a suitable nuclear reactor to irradiate 237Np targets, hot cells to separate plutonium from fission products and residual neptunium (~13% 238Pu yield) and facilities to recycle the neptunium back into targets (National Research Council, 2009). Consequently, in Europe, 241Am, which can be recovered from separated aged plutonium, is considered for this purpose as an accessible and cost-effective alternative to 238Pu. Due to the half-life of 241Pu (14.33 years), the build-up of 241Am takes some time, and it can be found in significant quantities in spent nuclear fuel with high or medium burn-ups after some years of storage. However, americium that is directly separated from the spent fuel does not only contain 241Am but also 243Am and 242mAm (in smaller amounts), which makes it less suitable and more difficult to employ for RPS, due to lower specific power and higher neutron emission rate. Isotopically pure 241Am, on the other hand, builds up over time by in-growth into existing stocks of separated Pu from reprocessing. This can be an issue for the handling and processing of the Pu when it is refabricated into new MOX fuel elements after several decades of storage, and especially if second-generation Pu from reprocessing of irradiated MOX fuel is used, where significant amounts of 241Pu were already created during the first recycling step. Table 3.1 shows exemplar isotopic compositions of Pu that was separated from spent nuclear fuel from a pressurised water reactor (PWR) after five years of irradiation of UO2 and MOX to a burn-up of 55 GWd/tHM each.Figure 3.5 shows that already after 30 years of storage circa 11 wt% to 14 wt% of the heavy metal are composed of 241Am, which needs to be chemically separated from the Pu before it can be refabricated into new fuel elements. On the other hand, the in-growth of 241Am is a positive feature with respect to the utilisation for RPS, as it constitutes a source of continuous supply of power, providing radioisotopes without the need to operate a dedicated reactor or to fabricate and process specific irradiation targets (Ambrosi et al., 2019).Table 3.1. Typical isotopic composition of Pu in spent nuclear fuel at the end of irradiationIsotopeHalf-life (years)Pu composition of irradiated UO2 (wt%)*Pu composition of irradiated MOX (wt%)**238Pu 87.73.454.41239Pu24 113.547.4530.81240Pu6 563.0425.1029.85241Pu14.3314.8718.59242Pu3.74E+059.1316.33Notes: Author calculation with WebKorigen, www.ites.kit.edu/235.php. * PWR irradiation of 4.0% enriched UO2 in 5 years to 55 GWd/tHM. ** PWR irradiation of MOX with 3.7% fissile Pu in 5 years to 55 GWd/tHM.Figure 3.5. Example calculation of build-up of 241Am in reprocessed Pu from UO2 and MOX irradiationSource: NEA EGFRW data, 2022.3.2.1. Reuse of 241Am for space applications in Europe3.2.1.1. BackgroundThe high isotopic power of 241Am makes it possible to use it in an innovative way in larger quantities: as a heat-providing isotope for radioisotope power systems (RPS) for space applications as an alternative to 238Pu, which is currently used in China, Russia and the United States. Given that this is an emerging and innovative use of americium based on recent developments since about 2010, it is described in greater detail in this section.In its Robotic Exploration Technology Plan from 2009 (ESA, 2011) the European Space Agency (ESA) identified RPS as a “key enabling technology” and decided to initiate an ESA-funded development programme for radioisotope thermoelectric generators (RTG) and radioisotope heater units (RHU) (Ambrosi et al., 2019; Summerer and Stephenson, 2011). Several isotope selection studies were performed as part of this programme, and 241Am was identified as a suitable isotope for the European RPS development (Summerer and Stephenson, 2011). Since then, “the maturity of the technology has reached a level that it can be incorporated in mission studies and roadmaps targeting the period from the mid-2020s onwards” (Ambrosi et al., 2019). A good overview of the status and progress of the European RPS development programme can be found in (Ambrosi et al., 2019). 3.2.1.2. Properties of 241Am relevant to applications for space powerMetallic americium is a silvery, soft material with a relatively low density of 13.67 g/cm³. It does not offer significant advantages compared to the oxide with respect to Am-atom density (+30%) and specific power (+13%). In addition, it melts at 1 176°C and undergoes phase transitions at 769°C and 1 077°C, which causes dimensional changes (Freis, 2020). Am-metal is also highly pyrophoric and oxidises quickly in air, which is an unwanted property with respect to safety in case of accidents and in post-accident environments. Therefore, the oxide is usually chosen for space power applications. The main properties of 241Am-metal and 241AmO2 are summarised in Table 3.2 and compared to the metal and oxide of 238Pu. Americium oxide is a hard ceramic material with a density of 11.68 g/cm³, which is compatible with the materials used for encapsulation and the potential operating or post-accident environments. The ceramic powder can be pressed and sintered into suitable pellets for RPS using conventional powder metallurgy equipment. However, the americium-oxygen system shows a complex behaviour with many phase transitions. Figure 3.6 illustrates the different crystalline phases as functions of temperature and stoichiometry. Table 3.2. Properties of 241Am and 238Pu as metal and oxideProperty241Am-metal241AmO2238Pu-metal238PuO2Half-life432.8 y87.7 yDensity13.67 g/cm³11.68 g/cm³19.85 g/cm³11.46 g/cm³Power density0.114 W/g0.101 W/g0.567 W/g0.500 W/gThermal conductivity10 W/m K~2.0 W/m K6-16 W/m K3-10 W/m KMelting point1 176°C2 113°C640°C2 744°CNote: Based on (Freis, 2020) and (Magill and Magill, 2010), see www.ites.kit.edu/235.php. Figure 3.6. Phase diagram of the Am-O systemSource: Based on (Gotcu-Freis, 2011), (Epifano, 2017) and (Konings and Stoller, 2020).The dioxide (AmO2) crystallises in the face centred cubic structure (α-phase, space group Fm3m), while the sesquioxide (Am2O3) exists in a hexagonal form (A-phase, space group P3m1) at temperatures above 700 K and O/Am ratios between 1.5 and 1.62, and in cubic form (C and C’-phase, space group Ia3) up to an O/Am ratio of 2, depending on the temperature (mixed Am(III)/Am(IV) structure). The melting point of AmO2 is assumed to be at 2 113°C (McHenry, 1965) but this value has a relatively high uncertainty because the dioxide loses oxygen above 1 100 K, and melting occurs in off-stoichiometric conditions, which makes it difficult to determine the exact melting point (Konings and Stoller, 2020). 3.2.1.3. Processes for 241Am recoveryMany different aqueous and non‐aqueous extraction methods were developed in the past to chemically separate and extract 241Am from nuclear spent fuel or stockpiles of plutonium (Runde and Schulz, 2010), mainly to recover americium from waste streams from civil or defence applications. The developed methods include techniques based on pyro-chemistry (Runde and Schulz, 2010), precipitation-based processes (Runde and Schulz, 2010), extraction chromatography (Umeda, 2004), solvent extraction (Umeda, 2004) or extraction by ion exchange (Navratil and Schulz, 1980). In the frame of the European RPS programme, the UK National Nuclear Laboratory (NNL) was contracted by ESA to develop an industrial process for separation of 241Am from PuO2 with an initial output target for a production facility of circa 9 kg per year, which would be sufficient for one RTG of circa 50 Wel (Brown et al., 2018). In the frame of this programme, NNL developed a new chemical process to purify the Pu and economically produce 241Am, the so-called americium and plutonium purification by extraction (AMPPEX) process (Brown et al., 2018; Ambrosi et al., 2019; Sarsfield, 2017). This process has the advantage of providing a high yield (>99%) and a product of high purity (>99%) (Brown et al., 2018; Sarsfield, 2017). In addition, it can be fitted into a relatively small footprint, complies with criticality control requirements and minimises the discharge of radioactive waste (Brown et al., 2018). This is now the leading European process option for 241Am recovery from aged plutonium and is described in more detail in Section 3.2.2. 3.2.2. The americium and plutonium purification by extraction (AMPPEX) processThe process used to extract americium from aged plutonium dioxide involves three main steps: dissolution of PuO2, separation of americium from plutonium and other impurities, and conversion of the pure americium solution into a solid oxide product. Details of the process development are available in references (Ambrosi et al., 2019) and (Brown et al., 2018) and are summarised below.3.2.2.1. DissolutionPlutonium dioxide is notoriously difficult to dissolve in nitric acid alone (Ryan and Bray, 1980) and to complete a dissolution batch in a reasonable amount of time requires more aggressive reagents. Hydrofluoric acid in nitric acid is often used, although this has implications for plant corrosion and alpha,n neutron emission doses to operators. Alternatively, silver (II) dissolution allows the aggressive nature of silver (II) ions to dissolve PuO2. Dissolution of aged UK PuO2 up to 200 g/L in ~4 mol/L HNO3 has been demonstrated using electrochemically generated Ag(II) ions in an electrochemical cell where anolyte and catholyte solutions are separated by a membrane; reactions have been followed in situ spectrophotometrically. One interesting result is that 20 g of aged PuO2 dissolved at a similar rate to 10 g of fresh PuO2, implying that americium may play a role in the dissolution process. Dissolution can be switched off through removal of the current and at the end of the cycle conditioning of the liquor with nitrogen oxide (NOx) is used to convert the Pu(VI) generated to Pu(IV), which is more suitable for solvent extraction-based separation processes.3.2.2.2. SeparationThe separation process is performed in two steps. The first step uses standard plutonium uranium reduction extraction (PUREX) solvent (30% v/v tributyl phosphate diluted in odourless kerosene [TBP/OK])) to extract the plutonium while the americium and silver remain in the aqueous phase. The second step uses a different solvent mixture of N,N,N′,N′ – tetraoctyl diglycolamide (TODGA) and a phase modifier N,N′ – dihexyloctanamide (DHOA) in a diluent (odourless kerosene) to selectively extract americium and leave silver in the aqueous phase, which can be recovered and recycled. Typical flowsheets are given by Jamie Brown and colleagues (Brown et al., 2018) and for the first cycle involve 12 centrifugal contactor stages to extract plutonium into the TBP/OK phase and scrub the organic product before 16 stages of stripping the plutonium at a lower acidity using a mixture of 0.5 mol/L hydroxylamine stabilised by 0.05 mol/L hydrazine. Americium and silver, along with some other trace elements, are directed to the aqueous raffinate from the first cycle. Plutonium recovery across this cycle is >99%. The second cycle also uses 12 centrifugal contactor stages of extract and scrub to separate the americium from silver by extraction into 0.15 mol/L TODGA (extractant) and 0.5 mol/L DHOA (phase modifier) in OK (diluent). Americium is backwashed in 12 stages with 0.01 mol/L HNO3 and there is an oxalic acid solvent wash (4 stages) to reduce residual alpha activity in the solvent. Very good performance of the flowsheet is observed with typically <0.1 mg/L of silver in the americium product and >99% recovery of americium. TODGADHOA3.2.2.3. FinishingThe americium nitrate solution generated from the separation process contains around 5 g/L americium at a low acidity (~0.5 mol/L HNO3) and can be fed directly into a continuous precipitator using oxalic acid to generate americium oxalate Am2(C2O4)3.xH2O as a pale yellow solid. Once washed and dried, the solid is decomposed in air to produce americium oxide. Figure 3.7. The AMPPEX process for separation of 241Am from aged PuO2Source: NEA EGFRW, 2023.The counter-current solvent extraction process used for separation coupled with the oxalate route as the finishing process provides high decontamination factors and, to date, multi-gram quantities of a pure (>99%) americium oxide powder product in high (>99%) yield have been produced. These have been used in the development of the next stage of the process in the envisaged manufacturing of americium-based space heat and power sources – pelletisation. Additionally, work is ongoing at the NNL to design a new facility for scaling up the AMPPEX process for americium separations with operations expected to start in 2027.3.2.2.4. PelletisationUnder different atmospheres and temperatures, americium oxide undergoes phase changes, which are accompanied by dimensional modifications and can lead to pellet disintegration (Freis, 2020; Vigier et al., 2018; Thiriet and Konings, 2003). AmO2 pellets, which are sintered under oxidising conditions will start to release oxygen under the operating conditions of the RPS in space (elevated temperatures and vacuum). This will cause the material to slowly transform into AmO2-x, thereby increasing its volume, and finally to convert into americium sesquioxide (Am2O3) (Guéneau et al., 2011; Sari and Zamorani, 1970; Vauchy et al., 2017). This process is accompanied by a structural reorganisation and change of density and can finally lead to pellet disintegration. On the other hand, americium oxide pellets are difficult to sinter under reductive conditions, and cracking can occur due to the structural reorganisation, which happens when AmO2 is converted into Am2O3 (Vigier et al., 2018; Sarsfield, 2017; Freis, 2020), and due to thermal stresses induced during heat-up by the anisotropic thermal expansion coefficient of americium sesquioxide (Vigier et al., 2018; Lebreton et al., 2012). In addition, Am2O3 is prone to oxidation and will change into AmO2 when stored in oxygen containing atmospheres and because of self-irradiation effects. This process can lead to complete pulverisation of the pellets. However, even if Am2O3-pellets can be successfully protected from oxygen before launch into space, any accident scenario inside earth’s oxygen containing atmosphere, like launch-pad explosion or earth re-entry accidents, will cause Am2O3 to transform into the dioxide and disintegrate, which can increase the dispersion of fine respirable particles into the atmosphere in case of cladding failure (Freis, 2020; Vigier et al., 2018). To stabilise americium dioxide in its cubic form under a wide range of atmospheres and temperatures, the European Commission’s Joint Research Centre (JRC) has developed a new synthesis and pelletisation route, based on the addition of a low amount of uranium dioxide (Vigier et al., 2018). Previous studies have shown that when uranium is mixed with different trivalent oxides, a charge compensation effect can be observed where the uranium is oxidised above the oxidation state IV even under reducing conditions (Butorin et al., 2017; Lebreton et al., 2015; Mayer et al., 1994; and Nishi et al., 2017). This effect stabilises the cubic phase even at low concentrations of uranium (Popa et al., 2016). By adding circa 12% of uranium oxide into aged americium oxide, containing 6% Np from decay and 2% Pu left-over from reprocessing, it was possible to successfully sinter several stable discs and pellets under moisturised Ar/H2 atmosphere. These included a prototype pellet with a mass of circa 3 g and the dimensions of the 238PuO2 pellets produced for the US Light Weight Radioisotope Heater Unit (LWRHU) (Tate, 1982) (height: 10 mm, diameter: 6 mm), and a prototype disc with a larger diameter of 15 mm, as designed for the future European RHU (Ambrosi et al., 2019) (see Figure 3.8).The stabilised material had the composition (Am0.80,U0.12,Np0.08,Pu0.02)O1.8 and showed a good sintering behaviour without phase changes, and the sintered discs and pellets were of good quality without cracks. In addition, the material showed a good structural and dimensional stability during storage as well as a good resistance against self-irradiation effects (Vigier et al., 2018). A long-term assessment of the crystallographic and macroscopic swelling behaviour was performed. It was observed that low crystallographic swelling occurred under alpha self-irradiation, which saturated at circa 0.15% increase of lattice parameter after 60 days (see Figure 3.9). No macroscopic swelling was observed. In addition, oxidation tests on sintered discs were performed, which showed that the material was stable up to 1 000°C (Vigier et al., 2018). Overall, these results showed a significant improvement for the safety against dispersion of radioactive material in case of accidents.Figure 3.8. (Am,U)O2 prototype pellet (left) and prototype disc (right)Source: Courtesy of the European Commission, Joint Research Centre, Karlsruhe, Germany.Figure 3.9. Crystallographic swelling of (Am,U)O2 under the effect of alpha self-irradiation (left) and weight change during oxidation test on (Am,U)O1.8 (right)Source: Vigier et al., 2018 – Further permission for use should be directed to the ACS Publications.Due to the insertion of uranium and the presence of Np and Pu in the starting material, the produced discs and pellets had a specific power of 0.082 W/g, which is significantly lower compared to 0.101 W/g for pure 241AmO2. This is also the main drawback for the use of uranium-doped americium oxide for space applications. Nevertheless, the doping of AmO2 with uranium results in several advantages with respect to material properties and safety, namely:good sintering behaviour due to the absence of structural changes and anisotropic thermal expansion;long-term stabilisation of the cubic structure and resistance towards the effects of alpha self-irradiation;low crystallographic swelling and no observable macroscopic swelling; andstability against oxidation under a broad range of conditions including temperatures up to 1 000°C.In addition, the cubic structure is a good host for the americium decay product 237Np, which is integrated into the material structure during its slow build-up over decades of RPS operation (Ambrosi et al., 2019; Freis, 2020; Vigier et al., 2018).3.2.3. Russian approaches to separation of isotopically pure 241Am from solutions after processing of aged plutoniumSection 3.2.2 focused on European approaches to recovery of 241Am from aged PuO2 for space power sources. However, other countries are also interested in the valorisation of 241Am for uses outside the nuclear fuel cycle, including Russia and the United States. In Russia, isotopically pure 241Am is used to create sources of fast neutrons, sources of gamma radiation and as a starting material to produce transcurium elements and biomedical 238Pu.To obtain 241Am, plutonium with a high content of 241Pu, aged for a long time, is used, during the b-decay of which 241Am is formed. Isolation of isotopically pure 241Аm is carried out at the Mayak Production Association only by the method of displacement complex-forming chromatography, and the obtained 241Аm has been used to satisfy the demand for it not only in the domestic market of Russia, but also internationally.To obtain the high-purity americium preparations from solutions of the complex composition, the displacement complexing chromatography (DCC) technique was used. Two-stage technology was used for the separation of isotopic pure 241Am in the amount of 50-100 g from solutions containing all elements of the rare earth group. The first stage was conducted for the efficient decontamination of americium from light and transition rare earth elements (REE) using the eluate containing 0.025 mol/L of diethylenetriaminepentaacetate (DTPA) and 0.015 mol/L of ammonium citrate. During the second stage the final end-polishing of americium from heavy REE was performed using the solution containing 0.073 mole/L nitroacetic acid (Kharitonov et al., 2010; Chuvaleva et al., 1996).In 1998, O.V. Kharitonov and colleagues (Kharitonov et al., 1998) presented results on the separation of isotopically pure 241Аm from solutions after the processing of aged plutonium by the DCC method. The isolation of 241Аm was carried out on two chromatographic units located at the Mayak Production Association. The first setup consisted of eight columns made of stainless steel; five chromatographic cycles of 241Аm isolation were carried out on it. The next three cycles of 241Am isolation were carried out on a facility located in the canyon, consisting of seven columns. The columns were filled with KU-2 sulfonic acid cation exchanger in hydrogen or nickel forms. Ammonium diethylenetriaminepentaacetate (DTPA) solution and DTPA solution containing ammonium citrate were used as an eluent. The elution was carried out at a temperature of 7080°C. The solution feed rate (4 ml/[min-cm2]) was controlled at the outlet of the column.The solution was supplied to the chromatographic stage after the dissolution of PuO2 in nitric acid, and after separation of the main mass of plutonium from americium on an anion exchanger. The approximate composition of the solution (mg/L) entering the chromatographic stage is presented below.Table 3.3. Composition of the solution entering the chromatographic stageElement or isotopeConcentration (mg/L)241Аm1 200239Pu286Се720Fe3 200Сr500Ni500Н+, mol/L0.22As a result, 241Am meets the technical requirements for the finished product. The americium content of the AmO2 product was 82%, indicating a chemical purity of not less than 94%.In the third cycle, the method of additional recovery of plutonium was tested at the stage of chromatographic purification of americium. The sorption of plutonium on KU-2 is carried out in the trivalent state in the presence of a reducing agent, hydrazine nitrate, and at a temperature of 50-60°C, and elution is carried out with a DTPA solution (0.0250.05 mol/L).3.3. ReferencesAmbrosi, R.M. et al. (2019), “European radioisotope thermoelectric generators (RTGs) and radioisotope heater units (RHUs) for space science and exploration”, Space Sci. Rev., Vol. 215: 55, HYPERLINK "https://doi.org/10.1007/s11214-019-0623-9"https://doi.org/10.1007/s11214-019-0623-9.Baron, P. et al. (2019), “A review of separation processes proposed for advanced fuel cycles based on technology readiness level assessments”, Progress in Nuclear Energy, Vol. 117, 103091, https://doi.org/10.1016/j.pnucene.2019.103091.Brown, J. et al. (2018), “Americium and plutonium purification by extraction (the AMPPEX process): Development of a new method to separate 241Am from aged plutonium dioxide for use in space power systems”, Progress in Nuclear Energy, Vol. 106, pp. 396-416, http://dx.doi.org/10.1016/j.pnucene.2018.02.008.Burney, G.A. (1964), “Ion exchange process for the recovery of 238Pu from irradiated 237Np”, Ind. Eng. Chem. Process Design Develop, Vol. 3: 329.Butorin, S.M. et al. (2017), “Characteristics of chemical bonding of pentavalent uranium in La-doped UO2”, Chem. Commun, Vol. 53, pp. 115-118, https://doi.org/10.1039/C6CC07684J.Chuvaleva, E.A, O.V. Kharitonov and L.A. Firsova (1996), “Separation of americium from rare earth elements by chromatographic method using separating ions”, Radiokhimia, Vol. 38, No. 5, pp. 438-441 (in Russian).Collins, E.D. (2015), “Advanced thermal denitration conversion processes for aqueous-based reprocessing and recycling of spent nuclear fuels”, Chap. 12, Reprocessing and Recycling of Spent Nuclear Fuel, Woodhead Publishing Series in Energy: Number 79, edited by R. Taylor, Elsevier.EASAC (2014), Management of Spent Nuclear Fuel and its Waste, EASAC, EASAC Policy Report no. 23, EASAC, Brussels, pp. 1-40, https://easac.eu/publications/details/management-of-spent-nuclear-fuel-and-its-waste-1.Epifano, E. et al. (2017), “Insight into the Am–O phase equilibria: A thermodynamic study coupling high-temperature XRD and CALPHAD modeling”, Inorganic Chemistry, Vol. 56 (13), pp. 7416-7432, https://doi.org/10.1021/acs.inorgchem.7b00572.ESA (2019), “Safety Policy on the Use of Nuclear Power Sources”, United Nations Office for Outer Space Affairs, UN: Paper A/AC.105/C.1/2019/CRP.10.ESA (2011), Robotic Exploration Technology Plan, Programme of Work 2009-2014, European Space Agency, https://sci.esa.int/s/wxPl0vw.Freis, D., J.-F. Vigier, K. Popa and R. Konings (2020), “Research in support of European radioisotope power system development at the European Commission’s Joint Research Centre in Karlsruhe”, ATW Int. J. Nucl. Power, Vol. 65, pp. 198-205, HYPERLINK "https://publications.jrc.ec.europa.eu/repository/handle/JRC120317"https://publications.jrc.ec.europa.eu/repository/handle/JRC120317.Geist, A. et al. (2020), “An overview of solvent extraction processes developed in Europe for advanced nuclear fuel recycling, part 1 – heterogeneous recycling”, Separation Science and Technology, Vol. 56, pp. 1866-1881, https://doi.org/10.1080/01496395.2021.2001531.Gogolski, J.M. and M.P. Jensen (2021), “Using N,N-dialkylamides for neptunium purification from other actinides for space applications”, Separation Science and Technology, Vol. 56(64), pp. 1-14, https://doi.org/10.1080/01496395.2020.1845209.Gotcu-Freis, P. et al. (2011), “A thermodynamic study of the Pu–Am–O system”, Journal of Nuclear Materials, Vol. 414 (3), pp. 408-421, https://doi.org/10.1016/j.jnucmat.2011.05.014. Groh, H.J. and C.S. Schlea (1970), “The recovery of 237Np and 238Pu”, Progress in Nuclear Energy, Series III, Process Chemistry, Vol. 4, pp. 507-547.Guéneau, C., A. Chartier and L. Van Brutzel (2011), “Thermodynamic and thermosphysical properties of the actinide oxides”, Chapter 2.02, Comprehensive nuclear materials, 2011, pp. 21-59, Elsevier.Kharitonov, O.V., E.A. Chuvaleva, V.M. Gelis and L.A. Firsova (1998), “Production of gram amounts of americium by displacement complexing chromatography. II. Isolation of isotope-pure 241Am from solutions after reprocessing of aged plutonium”, Radiokhimia, Vol. 4, no.2, pp 125-127 (in Russian).Kharitonov, O.V., L.A. Firsova, L.A., V.M. Gelis and V.A. Kozlitin (2010), “Features of chromatographic separation of rare earth elements and TPE on columns with successively decreasing diameter”, Voprosi radiatsionnoj bezopasnosty, 13-31 (in Russian).King, L.J., J.E. Bigelow and E.D. Collins (1981), “Experience in the separation and purification of transplutonium elements in the transuranium processing plant at Oak Ridge National Laboratory”, Transplutonium Elements – Production and Recovery, ACS Symposium Series 161, American Chemical Society.Konings, R.J.M. and R. Stoller (2020), Comprehensive Nuclear Materials, 2nd edition, Elsevier, San Diego, United States.Lange, R.G and W.P Carroll (2008), “Review of recent advances of radioisotope power system”, Energy Conversion and Management, Vol. 49, Issue 3, pp. 393-401, https://doi.org/10.1016/j.enconman.2007.10.028.Lebreton, F. et al. (2015), “Peculiar behavior of (U, Am) O2−δ compounds for high americium contents evidenced by XRD, XAS, and Raman spectroscopy”, Inorg. Chem, Vol. 54, pp. 9749-9760.Lebreton, F., R.C. Belin, T. Delahaye and P. Blanchart (2012), “In-situ Xray diffraction study of phase transformations in the Am−O system”, J. Solid State Chem, Vol. 196, pp. 217-224.Magill, J. and N.F. Magill (2010), “Nucleonica: A platform for organizational knowledge management in the nuclear domain”, Conference Proceedings: Proceedings of ENC 2010 European Nuclear Conference 30 May-2 June 2010, Barcelona, Spain, ENC Transactions, p. 44-48.Mayer, K., B. Kanellakopoulos, J. Naegele and L. Koch (1994), “On the valency state of americium in (U0.5Am0.5) O2−x”, J. Alloys Compd, Vol. 213-214, pp. 456-459.McHenry R.E. (1965), “Melting points of curium and Americium oxides”, Transactions of the American Nuclear Society, Vol. 8.Mowafy, E.A. and H.F. Aly (2007), “Synthesis of some N, N, N’, N’–Tetraalkyl–3–Oxa-Pentane–1,5- Diamide and their applications in solvent extraction”, J. Solv. Extr. and Ion Exch, (25) 205-224.Myrick, R.E. and R.L. Folger (1964), “Fabrication of targets for neutron irradiation of neptunium Dioxide”, Ind. Eng. Chem. Process Design Develop, Vol. 3: 309.National Research Council (2009), Radioisotope Power Systems: An Imperative for Maintaining U.S. Leadership in Space Exploration, The National Academic Press, Washington DC.Navratil, J.D. and W.W. Schulz (1980), Transplutonium Elements, Production and Recovery, Chemical Congress of the North American Continent, American Chemical Society, Washington DC.NEA (2021), Strategies and Considerations for the Back End of the Fuel Cycle, OECD Publishing, Paris, www.oecd-nea.org/jcms/pl_55928. NEA (2018), State-of-the-Art Report on the Progress of Nuclear Fuel Cycle Chemistry, OECD Publishing, Paris, www.oecd-nea.org/jcms/pl_14970. NEA (2012), Curium Management Studies in France, Japan and USA, OECD Publishing, Paris, www.oecd-nea.org/jcms/pl_19108.NEA (2010), National Programmes in Chemical Partitioning: A Status Report, OECD Publishing, Paris, www.oecd.org/publications/national-programmes-in-chemical-partitioning-9789264106871-en.htm.Netter, P. (2012), “16 – Reprocessing of spent oxide fuel from nuclear power reactors”, in: I. Crossland (Ed.), Nuclear Fuel Cycle Science and Engineering, Woodhead Publishing, pp. 459-500, https://doi.org/10.1533/9780857096388.4.459.Nishi, T., M. Nakada and M. Hirata (2017). “Lattice parameter functions of (AmyU1−y) O2−x based on XRD and XANES measurements”, J. Solid State Chem., Vol. 256, pp. 252−255, https://doi.org/10.1016/j.jssc.2017.09.011.Popa, K. et al. (2016), “Further insights into the chemistry of the Bi-U-O system”, Dalton Trans., Vol. 45, pp. 7847-7855, https://doi.org/10.1039/C6DT00735J.Porter, J.A. (1964), “Production of neptunium dioxide”, Ind. Eng. Chem. Process Design Develop, Vol. 3, p. 289, https://doi.org/10.1021/i260012a001.Ryan, J.L. and L.A. Bray (1980), “Dissolution of plutonium dioxide – A critical review”, Actinide Separations, Navratil J.D., and W.W. Schulz (Eds.), 499-514, ACS Symposium Series 117.Runde, W.H. and W.W. Schulz (2010), “Americium”, The Chemistry of the Actinide and Transactinide Elements, pp. 1265-1395, Springer, Dordrecht, https://doi.org/10.1007/1-4020-3598-5.Sari, C. and E. Zamorani (1970), “An investigation in the americium oxide system”, J. Nucl. Mater., Vol. 37, pp. 324-330, HYPERLINK "https://doi.org/10.1016/0022-3115(70)90162-5"https://doi.org/10.1016/0022-3115(70)90162-5.Sarsfield, M.J. et al. (2017), “The separation of 241Am from aged plutonium dioxide for use in radioisotope power systems”, E3S Web of Conferences, EDP Sciences.Schulz, W.W. and G.A. Benedict (1972), Neptunium-237 Production and Recovery, US Atomic Energy Commission Office of Information Services, United States.Street Jr, K. and G.T. Seaborg (1950), “The separation of americium and curium from the rare earth elements”, Journal of the American Chemical Society, Vol. 72 (6), pp. 2790-2792, https://doi.org/10.1021/ja01162a530.Summerer, L. and K. Stephenson (2011), “Nuclear power sources: A key enabling technology for planetary exploration”, Proceedings of the Institution of Mechanical Engineers, Part G: Journal of Aerospace Engineering, pp. 129-143, https://doi.org/10.1243/09544100JAERO766.Tate, R.E. (1982), The Light Weight Radioisotope Heater Unit (LWRHU): A Technical Description of the Reference Design, LANL report – LA_9078_MS, Los Alamos, United States.Taylor, R (2015), Reprocessing and Recycling of Spent Nuclear Fuel, 1st edition ed., Woodhead Publishing, Oxford, https://doi.org/10.1016/C2013-0-16483-5.Taylor, R., W. Bodel, L. Stamford and G. Butler (2022), “A review of environmental and economic implications of closing the nuclear fuel cycle Part 1: Wastes and environmental impacts”, Energies, Vol. 15 (4), 1433, https://doi.org/10.3390/en15041433.Thiriet, C., and R.J.M. Konings (2003), “Chemical thermodynamic representation of AmO2−x”,J. Nucl. Mater., Vol. 320, pp. 292-298, HYPERLINK "https://doi.org/10.1016/S0022-3115(03)00188-0"https://doi.org/10.1016/S0022-3115(03)00188-0.Umeda, M. et al. (2004), “Separation of americium from Plutonium-solvent extraction raffinate by extraction chromatography using TODGA adsorbent”, International conference ATALANTE 2024, Nîmes, France, No. INIS-FR-3040, Tokai Establishment.Vauchy, R., A. Joly and C. Valot (2017), “Lattice thermal expansion of Pu1 yAmyO2 x plutonium-americium mixed oxides”, J. Appl. Crystallogr., Vol. 50, pp. 1782-1790, HYPERLINK "https://doi.org/10.1107/S1600576717014832"https://doi.org/10.1107/S1600576717014832.Vigier, J.F. et al. (2018), “Optimization of uranium-doped americium oxide synthesis for space application”, Inorganic chemistry, Vol. 57 (8), pp. 4317-4327, https://doi.org/10.1021/acs.inorgchem.7b03148.Wham, R.M. et al. (2015), “Reestablishing the supply of plutonium 238”, Proceedings of American Institute of Aeronautics and Astronautics (AIAA) Conference.Wigeland, R. et al. (2014), Nuclear Fuel Cycle Evaluation and Screening – Final Report, FCRD-FCO-2014-000106, INL/EXT-14-31465, 2014, pp. 1-51, Fuel Cycle Research and Development, United States Department of Energy, Idaho National Laboratory, United States.4. Group 1 and 2 elementsSeparation of the highly radioactive heat generating isotopes of caesium and strontium (mainly 137Cs and 90Sr), as well as uranium and plutonium from reprocessing and minor actinide partitioning and transmutation can lead to substantial reductions in the heat-generating potential of the residual high-level waste and, therefore, the size of a deep geological repository (NEA, 2021). To realise these benefits, the separated Cs and Sr would have to be immobilised and decay stored for up to 300 years before disposal. There have consequently been various studies to develop separation processes for Cs and Sr from high-level waste to reduce the waste burden on the repository (Xu et al., 2012; Collins et al., 2011) but there have also been various reports of recovering Cs and Sr (using similar chemistries) for other applications of their radioactivity and heat. The latter scenario is relevant to this report and discussed below. 4.1. CaesiumCs was recovered from high-level waste (HLW) generated during plutonium production at the Hanford Site in the United States (Barton et al., 1987). Two general categories of feed materials were processed to recover Cs: (1) alkaline tank waste liquids produced by neutralising acidic HLW for storage in carbon steel waste tanks, and (2) plutonium uranium reduction extraction (PUREX) acid waste. Ion exchange was used to recover Cs from the alkaline tank waste liquid. Zeolite type inorganic ion exchangers were first used, but these proved to be chemically unstable in the alkaline feed solutions. Subsequently, the organic ion exchange resin Duolite ARC-359 was used to recover Cs from the alkaline tank waste liquid. The Cs recovery from alkaline Hanford tank waste is of historical interest, but is not particularly relevant to any future recovery of Cs from spent fuel because the practice of neutralising highly acidic HLW is unlikely to be repeated.Cs recovery from the PUREX acid waste may be more relevant to any future scenario to recover Cs from spent fuel. In this case, the Cs was precipitated from solution by addition of phosphotungstic acid (Barton et al., 1987). The Cs-containing solids were collected by centrifugation and washed with aqueous sodium gluconate to remove metallic impurities. The solids were dissolved in sodium hydroxide solution and the Cs separated by ion exchange in a manner like the tank waste liquid. However, in this case the volume of material requiring processing was much less because of the preconcentration achieved in the phosphotungstate precipitation step.In the United Kingdom, a Caesium Extraction Plant (CEP) was built at Sellafield in the mid-1950s as part of the UK civil nuclear power programme. The plant was designed as a pilot plant to primarily produce 137Cs sources for radiotherapy purposes, using the highly active liquor from Sellafield reprocessing operations as the feedstock. The plant only operated until 1958, when faults developed in the evaporators within the plant and blockages occurred within the lines; the plant therefore became inoperable and was shut down. During its active life the plant produced twelve 1 kCi 137Cs and two or three 90Sr sources. The caesium was recovered from the HAL in a manner like that described by W.B. Barrton and colleagues (Barton et al., 1987). Liquor was initially concentrated in an evaporator prior to transfer into a precipitator vessel. In the precipitator vessel, each batch was diluted with water then treated with phosphotungstic acid solution, causing precipitation of caesium phosphotungstate. The precipitate was washed with 1 mol/L nitric acid then dissolved in 10% sodium hydroxide solution, before being reacidified to reprecipitate the caesium phosphotungstate. The precipitate was washed three times with 1 mol/L sulphuric acid then dissolved in 4 mol/L ammonium hydroxide solution. The resulting solution was transferred via a holding pot to an ion exchange column, which absorbed the phosphate and tungstate ions. The resulting ammoniacal solution of caesium carbonate from the column flowed into a second evaporator where it was concentrated 12 times to remove the ammonia. The resulting solution was neutralised to form caesium sulphate solution. This solution was finally transferred into a platinum funnel, sealed by a gold bung at its base, then heated to dryness. The funnel, containing the dried caesium sulphate, was assembled over a platinum capsule, and then placed in a furnace heated to 1 100ºC. In the furnace both the caesium sulphate and the gold foil melted, leaving the salt cast into the capsule. The capsule was sealed with a platinum plug.More recently, caesium and strontium were removed as a group from dissolved irradiated fuel solutions during demonstrations of the uranium extraction (UREX)+ suite of fuel partitioning options (Regalbuto, 2011). Two solvent extraction processes were tested: (1) the chlorinated cobalt dicarbolide-polyethylene glycol (CCD-PEG) process (Law et al., 2004), and (2) the fission product extraction (FPEX) process (Riddle et al., 2005). Both methods were successfully demonstrated to separate Cs and Sr from the UREX process raffinate (Pereira et al., 2007); however, FPEX is viewed as preferable because the aliphatic hydrocarbon diluent used is compatible with likely upstream and downstream processes compared to the phenyltrifluoromethyl sulfone (FS-13) diluent used in the CCD-PEG system (Regalbuto, 2011). Separation of the Cs from Sr was not demonstrated, so that step requires development if Cs and Sr are to be isolated as pure products.While most 137Cs gamma irradiators have been based on caesium salts sealed in metal containers, India has taken the international lead in having the caesium in a vitrified form i.e. as a glass “irradiation pencil”, which therefore avoids the concerns about a potentially dispersible caesium salt. In the Indian process, radioactive caesium is recovered from high-level liquid waste (HLLW) as caesium nitrate and then immobilised in sodium borosilicate glass and poured into a primary stainless steel tube with a diameter of 23 mm and overall length of 204 mm, giving a total caesium activity of ~300 Ci per pencil. This pencil, with a specific activity of 2 Ci/gm of glass, qualifies as an irradiation pencil for blood irradiation (Wattal, 2017).The caesium recovery is based on solvent extraction using 1,3-dioctyloxycalix [4] arene-crown-6 (CC6)/n-dodecane modified with isodecyl alcohol (Sharma et al., 2014).For a period, gamma irradiators based on 137Cs were less favoured than those built with 60Co. This was mainly due to the ease of production of 60Co in metallic form with high specific activity and four-times higher gamma energy than 137Cs. However, the six-times longer half-life of 137Cs compared with 60Co (approximately 30 years compared with 5 years) means that sources must be changed much less frequently with the consequently reduced dose to operators.4.2. StrontiumLike Cs, Sr was also recovered from Hanford HLW. In this case, Sr was first co-precipitated with a lead sulphate carrier. The sulphate precipitate was metathesised to the corresponding carbonate by treatment with Na2CO3, which was then dissolved in an acetate buffer at pH 4.7. Ethylenediaminetetraacetate (EDTA) or diethylenetriamine-N,N,N',N'',N''-pentaacetate (DTPA) was added to complex iron, lead and transition metal fission products, then the Sr was extracted with bis-(2-ethylhexyl) phosphoric acid (HDEHP) (Schulz et al., 1963). Although this process was successfully deployed industrially at Hanford, it resulted in the production of a highly hazardous complexant-containing waste that is some of the most challenging material to process and dispose of in the current Hanford environmental remediation effort.As mentioned in the preceding section, the CCD-PEG and FPEX processes were demonstrated with irradiated fuel for recovering Sr and Cs together, but separation of Sr from Cs was not demonstrated. Horwitz et al. reported the development of the strontium extraction (SREX) process for recovery of Sr from HNO3 media (Horwitz et al., 1991). The SREX system employs di-t-butylcyclohexano-18-crown-6 dissolved in 1-octanol to extract Sr according to the following equation (CE = the crown ether extractant):Sr2+(aq) + 2NO3–(aq) + CE(org) ⇌ [Sr(NO3)2(CE)](org)(1)This equilibrium allows Sr to be extracted at high nitrate concentration (molar concentrations of HNO3) with the nitrate ion shifting the reaction to the right. Decreasing the nitrate concentration results in shifting the reaction to the left so that Sr can be easily stripped into dilute HNO3. The SREX process has not been demonstrated for recovery of Sr from commercial spent fuel, but it has been investigated for removal of Sr from Hanford tank sludges dissolved in HNO3 (Lumetta et al., 1995) and calcined waste at the Idaho National Laboratory (INL) (US DOE, 1998). The chemistry described in Equation 1 forms the basis for a commercially available extraction chromatography resin used for analytical separations of Sr.Alongside its regime for recovery of 137Cs, India has also developed a process for the selective separation of 90Sr from high-level waste solution of high salt using 4,4′(5′)-[di-tert-butyldicyclohexano]-18-crown-6 (DtBuCH18C6) dissolved in an industrial diluent system: isodecyl alcohol + n-dodecane. The process solvent is optimised as 0.1 mol/L DtBuCH18C6 + 50% isodecyl alcohol/n-dodecane for satisfactory extraction of strontium at higher nitric acid concentrations (D4-8 M HNO3 = 5–14) (Sharma et al., 2019).90Sr has wide applications as a radiation source in radiotherapy, as a source of radionuclide 90Y (daughter product of 90Sr) for radiopharmaceutical applications and is increasingly being considered as a compact power source for space and other remote locations.4.3. ReferencesBarton, W.B., M.E. Johnson and L.A. Gale (1987), “Sixteen years of caesium recovery processing at Hanford’s B Plant”, in I.M. Leonard and E.J. Mayer, J.M. Pope (Eds.) Spectrum '86: Proceedings of the American Nuclear Society International Topical Meeting, Niagara Falls, New York, pp. 1126-1136.Collins, E.D., G.D. Del Cul and B.A. Moyer (2011), “8 – Advanced reprocessing for fission product separation and extraction”, in K.L. Nash, G.J. Lumetta (Eds.) Advanced Separation Techniques for Nuclear Fuel Reprocessing and Radioactive Waste Treatment, Woodhead Publishing, 2011, pp. 201-228.Horwitz, E.P., M.L. Dietz and D.E. Fisher, (1991), “SREX: A new process for the extraction and recovery of strontium from acidic nuclear waste streams”, Solvent Extraction and Ion Exchange, Vol. 9(1), pp. 1-25, https://doi.org/10.1080/07366299108918039. Law, J.D., R. Herbst, D. Peterman, R. Tillotson and T. Todd (2004), “Development of a cobalt dicarbollide/polyethylene glycol solvent extraction process for separation of cesium and strontium to support advanced aqueous reprocessing”, Nuclear Technology, Vol. 147, pp. 284-290, https://doi.org/10.13182/NT04-A3532.Lumetta, G.J., M.J. Wagner and E.O. Jones (1995), “Separation of Strontium-90 from Hanford high-level radioactive waste”, Separation Science and Technology, Vol. 30, pp. 1087-1101, https://doi.org/10.1080/01496399508010334.NEA (2021), Strategies and Considerations for the Back End of the Fuel Cycle, OECD Publishing, Paris, https://oecd-nea.org/jcms/pl_55928.Pereira, C. et al. (2007), “Lab-Scale demonstration of the UREX+1a process using spent nuclear fuel”, Waste Management 2007, Waste Management, Tucson, Arizona, United States.Regalbuto, M.C. (2011), “Alternative separation and extraction: UREX+ processes for actinide and targeted fission product recovery”, in K.L. Nash and G.J. Lumetta (Eds.) Advanced Separation Techniques for Nuclear Fuel Reprocessing and Radioactive Waste Treatment, Woodhead Publishing, Oxford, pp. 176-200.Riddle, C.L et al. (2005), “Fission product extraction (FPEX): Development of a novel solvent for the simultaneous separation of strontium and cesium from acidic solutions”, Solvent Extraction and Ion Exchange, Vol. 23, pp. 449-461, https://doi.org/10.1081/SEI-200058035.Schulz, W.W., J.E. Mendel and G.L. Richardson (1963), “Solvent extraction recovery and purification of Strontium-90”, Industrial and Engineering Chemistry Process Design and Development, Vol. 2, pp. 134-140, https://doi.org/10.1021/i260006a009.Sharma, J.N. et al. (2019), “Separation of strontium-90 from a highly saline high level liquid waste solution using 4,4′(5′)-[di-tert-butyldicyclohexano]-18-crown-6 + isodecyl alcohol/n-dodecane solvent”, Separation and Purification Technology, Vol. 229, https://doi.org/10.1016/j.seppur.2019.04.032.Sharma, J.N. et al. (2014), “Process development for separation of cesium from acidic nuclear waste solution using 1,3-dioctyloxycalix[4]arene-crown-6 + isodecyl alcohol/n-dodecane solvent”, Separation and Purification Technology, Vol. 135, pp. 176-182, https://doi.org/10.1016/j.seppur.2014.08.016.USDOE (1998), TRUEX/SREX Demonstration, United States Department of Energy, United States.Wattal, P.K. (2017), “Back end of Indian nuclear fuel cycle – A road to sustainability”, Progress in Nuclear Energy, Vol. 101, https://doi.org/10.1016/j.pnucene.2017.03.004.Xu, C., J. Wang and J. Chen (2012), “Solvent extraction of strontium and caesium: A review of recent progress”, Solvent Extraction and Ion Exchange, Vol. 30, pp. 623-650, https://doi.org/10.1080/07366299.2012.700579.5. Noble gases5.1. XenonSpent nuclear fuel contains significant quantities of noble gases including krypton (Kr) and xenon (Xe). There is little potential commercial value in the Kr because the primary isotope present, 85Kr, is radioactive. However, spent nuclear fuel (SNF) contains significant quantities of stable 136Xe, which has significant potential commercial value. Xenon is used in various applications, including deposition and etching in the semiconductor industry, (Yamawaki et al., 2007) building and automotive lighting, propulsion systems for deep space craft (Choueiri, 2009), and a variety of medical applications (Dingley et al., 2001; Esencan et al., 2013). This is illustrated in Figure 5.1.Figure 5.1. Production and uses of xenonSource: Courtesy of Pacific Northwest National Laboratory.Xenon exists in low concentrations in the atmosphere and is thus an expensive commodity collected by cryogenic distillation. Efficient separation of Xe from the off-gas from SNF processing facilities may offer a new source of relatively inexpensive Xe.The topic of Xe separation and storage has recently been reviewed, with a focus on physisorption-based separation methods as an alternative to cryogenic methods ADDIN EN.CITE <EndNote><Cite><Author>Banerjee</Author><Year>2018</Year><RecNum>1169</RecNum><DisplayText>(Banerjee, Simon et al. 2018)</DisplayText><record><rec-number>1169</rec-number><foreign-keys><key app="EN" db-id="e0sa0v959z2x56eztp7xv9w3zvev5sxxxztt" timestamp="1645719189">1169</key></foreign-keys><ref-type name="Journal Article">17</ref-type><contributors><authors><author>Banerjee, D.</author><author>Simon, C. M</author><author>Elsaidi, S. K.</author><author>Haranczyk, M.</author><author>Thallapally, P. K.</author></authors></contributors><titles><title>Xenon Gas Separation and Storage Using Metal-Organic Frameworks</title><secondary-title>Chem</secondary-title></titles><periodical><full-title>Chem</full-title></periodical><pages>466-494</pages><volume>4</volume><dates><year>2018</year></dates><urls></urls></record></Cite></EndNote>(Banerjee et al., 2018). Activated carbon is an inexpensive sorbent that has been shown to have favourable sorption capacity for Xe; however, exposure of activated carbon to the highly oxidising NOx present in nuclear fuel processing off-gas systems poses an unacceptable fire risk. Zeolites represent a class of robust inorganic materials that have favourable properties for deployment in fuel reprocessing facilities. Zeolites that have been impregnated with, or cation exchanged with, silver display good uptake of Xe and excellent selectivity for Xe over Kr. A disadvantage of the zeolite absorbents is the need to remove CO2 and H2O upstream because these species also have high affinity for the zeolitic sorption sites resulting in poor selectivity towards Xe. Further, both activated carbon and zeolites require large amounts of material to separate Xe due to their low capacities. Therefore, advanced functional materials are required to improve the adsorption capacity and selectivity towards Xe at near room temperature as an alternative to cryogenic distillation.Recently, a new class of advanced functional materials (porous organic cages, metal organic frameworks and covalent organic frameworks) were discovered that are promising as regards noble gas separation due to their synthetic tunability, high surface area, high adsorption capacity, selectivity and self-adjustable pore sizes, among other qualities. For example, porous organic cages (POCs) combine highly desirable properties such as uniform micropores, high surface areas, and thermal and chemical stability, making them highly appealing candidates for molecular gas separations. Typically, POCs are formed by a [4+6] cycloimination reaction. Depending on the amine and trialdehyde precursors, different cages have been synthesised. POCs synthesised from 1,3,5-triformylbenzene and 1,2-diaminocyclohexane have shown an exceptional selectivity towards Xe at room temperature under simulated reprocessing conditions. This was explained by the fact the pore diameter in POC is a perfect match for Xe molecular diameter (Chen et al., 2014; Patil et al., 2016).Like POCs, metal-organic-frameworks (MOFs) present a highly flexible platform for developing materials for selective gas separation and storage. For this reason, MOFs have been of special interest in developing materials for Xe separation from nuclear fuel reprocessing off-gas streams and its subsequent storage (Banerjee et al., 2018). UiO-66 represents a class of MOFs with high specific surface area with exceptional chemical and thermal stability. UiO-66 displays a Xe capacity of 1.58 mmol/g at 303 K and 1 bar pressure, and its Xe/Kr selectivity under dynamic conditions is 3.8. The open metal site MOF, HKUST-1, displays a Xe loading capacity of 3.3 mmol/g and a Xe/Kr selectivity of 2-3 under dynamic conditions typical of nuclear fuel processing off-gas. The open metal site material Ni-MOF-74 was shown to have even higher Xe capacity at 4.19 mmol/g; its Xe/Kr selectivity was calculated to be 7.3. However, one potential disadvantage of the MOFs with open metal sites is interference from water for interaction with the open metal site. This can drastically decrease the Xe uptake. Several factors are known to influence the selectivity of MOFs for noble gases. For example, MOFs with unsaturated open metal sites offer stronger adsorbate – MOF interactions; however, these adsorbents are not selective for noble gases when other competing gases (H2O, CO2 and N2) are present. Similarly, other MOF attributes studied include ligand polarisability, hydrophobicity, pore size, presence of metal nanoparticles, defects and temperature. All these factors play a significant role in the ability of these materials to separate noble gases from off-gases released from nuclear reprocessing conditions. Given the large number of MOFs, it is difficult to synthesise and test these materials for noble gas adsorption and separation. Therefore, predictive modelling tools are desirable.A new Xe selective MOF, calcium–4,4'–sulfonyl dibenzoate (CaSDB), was identified through a computationally inspired materials discovery approach. This CaSDB MOF was shown to have the highest reported Xe uptake and selectivity at room temperature under conditions relevant to nuclear reprocessing and waste form development applications. The CaSDB constructed from sulfonyldibenzoate (SDB) and CaO clusters was pinpointed to be highly Xe-selective by molecular simulations in a database containing 5 000 experimental and 125 000 hypothetical MOFs. The computational prediction was confirmed by conducting laboratory experiments that showed the highest Xe/Kr selectivity of 16 in presence of other gases including CO2 and humidity. To understand the high selectivity of CaSDB towards Xe, in situ single crystal X-ray diffraction experiments were carried out by flowing Xe and Kr while continuously collecting the diffraction data. The crystallographic analysis suggests the Xe atoms occupy the mid-point of the channels interacting with pore walls of the framework. CaSDB was tested under prototypic nuclear fuel processing conditions (1 300 ppm Xe, 130 ppm Kr balanced with air) at near room temperature; under these conditions CaSDBB MOF displays a Xe uptake of ~33 mmol/kg and excellent Xe/Kr separation performance. It retains Xe uptake properties even in the presence of 48% relative humidity, verifying its potential utility in off-gas streams containing water. Under slightly lower temperature (0°C) the capacity of the CaSDB MOF was shown to double under identical conditions. A two-column approach using CaSDB was demonstrated where bed 1 selectively removed Xe at room temperature from a gas mixture. The off-gas mixture (without Xe) exiting bed 1 was passed through bed 2, containing CaSDB at room temperature, to remove Kr. Very recently, the notion of using MOFs with self-adjusting frameworks has been pursued for Kr and Xe capture (Niu et al., 2022). These materials, exemplified by the MOF ATC-Cu, can adjust their pore size to accommodate target gases (e.g. Kr and Xe), yet exclude undesired species (e.g. N2 and O2) at normal temperature and pressure. Under flow conditions prototypic of nuclear fuel reprocessing off-gas (400 ppm Xe, 40 ppm Kr, 21% O2, balanced with N2 at 298 K and 1 bar), ATC-Cu displayed excellent separation of Xe, with a loading of 32 mmol Xe/kg achieved. This approach opens potentially new avenues to develop efficient Xe separation and storage materials.5.2. KryptonKrypton-85 (t1/2 = 10.7 years) is the primary radioisotope of Kr present in SNF, but it is accompanied by stable isotopes, especially those of atomic mass 83, 84, and 86. Separation of Kr is complicated by the presence of Xe, which is present at a concentration (molar basis) of about 10 times that of Kr. The greater polarisability of Xe results in it being more chemically reactive than Kr and thus Xe tends to be more competitive towards sorption than Kr. For this reason, an initial separation of Xe from the fuel processing off-gas (see Section 5.1) is desirable to simplify the capture of Kr. Good summaries of the methods available for Kr capture can be found in (Soelberg et al., 2013) and the K. Coldsnow dissertation (Coldsnow, 2017).Cryogenic distillation is the most mature technology for separating Xe and Kr from nuclear fuel processing off-gas streams (Soelberg et al., 2013). The method relies on condensation of the gaseous species at cryogenic temperatures, followed by fractional distillation to separate the individual components. The primary barrier to implementation of cryogenic distillation is its cost in implementation in a nuclear facility, but it also has safety hazards that must be mitigated such as avoiding condensation of reactive species (e.g. ozone). For these reasons, research over the last few decades has focused on developing sorption technologies for Kr capture.Activated carbon is a well-known material for capturing Xe and Kr. Fire safety is the primary concern that prevents use of activated carbon for this purpose, particularly the potential exposure of the activated carbon bed to strong oxidants such as NOx evolved during fuel dissolution. Other carbonaceous materials such as single-walled carbon nanotubes have also shown promise as Kr sorbents (Coldsnow, 2017), but presumably these suffer the same safety concerns as activated carbon. Inorganic sorbents offer the advantage of high chemical and radiolytic stability, and thus offer significant safety advantages over the carbon-based sorbents. Proton-exchanged mordenite has shown promise in the capture of Kr of fuel reprocessing off-gas streams. An engineered form of this material showed a capacity of 100 mmol Kr/kg sorbent for sorption from a Kr/He mixture at 190 K. However, the Kr capacity dropped to 7.4 mmol/kg for absorption from a Kr/Xe/air mixture that is more prototypic of what would be encountered in a nuclear fuel reprocessing facility (Garn et al., 2013). Again, this illustrates the need to selectively remove Xe prior to Kr capture. The same work demonstrated the potential of silver mordenite in separating Xe. The Xe sorption capacity was reported to be 28 mmol/kg sorbent from a Kr/Xe/air mixture at ambient temperature, with no detectable sorption of Kr under these conditions. At 191 K, the Xe capacity was 468 mmol/kg while the Kr capacity was 5.25 mmol/kg (Xe/Kr separation factor of approximately 90). So, one potential approach is to separate the Xe with silver mordenite, then capture Kr using the proton-exchanged mordenite.MOFs have also received considerable attention for application in the separation of Xe and Kr from nuclear fuel processing off-gas effluents. The MOFs offer the possibility to tune the size of the active sorption site to accommodate the target component for separation. A recent report has demonstrated the extension of this idea to create “smart” MOF materials that can self-adjust their structure to accommodate the target component to be separated while excluding other components ADDIN EN.CITE <EndNote><Cite><Author>Niu</Author><Year>2022</Year><RecNum>1176</RecNum><DisplayText>(Niu, Fan et al. 2022)</DisplayText><record><rec-number>1176</rec-number><foreign-keys><key app="EN" db-id="e0sa0v959z2x56eztp7xv9w3zvev5sxxxztt" timestamp="1646084810">1176</key></foreign-keys><ref-type name="Journal Article">17</ref-type><contributors><authors><author>Niu, Z.</author><author>Fan, Z.</author><author>Pham, T.</author><author>Verma, G.</author><author>Forrest, K. A.</author><author>Space, B.</author><author>Thallapally, P. K.</author><author>Al-Enizi, A. M.</author><author>Ma, S.</author></authors></contributors><titles><title>Self-Adjusting Metal-Organic Framework for Efficient Capture of Trace Xenon and Krypton</title><secondary-title>Angewandte Chemie</secondary-title></titles><periodical><full-title>Angewandte Chemie</full-title><abbr-1>Angew. Chem.</abbr-1></periodical><pages>e202117808</pages><dates><year>2022</year></dates><urls></urls><electronic-resource-num>10.1002/anie.202117807</electronic-resource-num></record></Cite></EndNote>(Niu et al., 2022). In this regard, a copper-based MOF (ATC-Cu; “ATC” refers to 1,3,5,7-adamantane tetracarboxyate) has been developed. The ATC-Cu material is selective for Xe over Kr, but it does have substantial capacity for Kr. A concept was proposed to operate a tandem system in which the Xe is first separated, followed by Kr. Proof-of-principle column breakthrough experiments were performed using a prototypic off-gas stream containing 400 ppm Xe, 40 ppm Kr and 21% O2, balanced with N2 at 298 K and 1 bar. Exceptional performance for both Xe and Kr capture were obtained, compared to other MOF materials that have been tested for this purpose.5.3. ReferencesBanerjee, D. , C. Simon, S. Elsaidi, M. Haranczyk and P. Thallapally (2018), “Xenon gas separation and storage using metal-organic frameworks”, Chem, Vol. 4, pp. 466-494, https://doi.org/10.1016/j.chempr.2017.12.025.Chen, L.J. et al. (2014), “Separation of rare gases and chiral molecules by selective binding in porous organic cages”, Nature Materials, Vol. 13, pp. 954-960, https://doi.org/10.1038/nmat4035.Choueiri, E.Y. (2009), “The efficient future of deep-space travel – Electric Rockets”, Scientific American, Vol. 300, pp. 58-65.Coldsnow, K. (2017), Capture of Radioactive Iodine and Krypton from Nuclear Off-Gas Streams with a Novel Sorbent, Master of Science, University of Idaho.Dingley, J. et al. (2001), “A closed xenon anesthesia delivery system”, Anesthesiology, Vol. 94, pp. 173-176, https://doi.org/10.1097/00000542-200101000-00034.Esencan, E. et al. (2013), “XENON in medical area: emphasis on neuroprotection in hypoxia and anesthesia”, Medical Gas Research, Vol. 3(4), http://dx.doi.org/10.1186/2045-9912-3-4.Garn, T.G., M.R. Greenhalgh and J.D. Law (2013), “Novel Sorbent Development and Evaluation for the Capture of Krypton and Xenon from Nuclear Fuel Reprocessing Off-Gas Streams”, GLOBAL 2013, Salt Lake City, Utah, American Nuclear Society: 1560-1566.Niu, Z. et al. (2022), “Self-Adjusting Metal-Organic Framework for Efficient Capture of Trace Xenon and Krypton”, Angewandte Chemie, Vol. 61, Issue 11, https://doi.org/10.1002/anie.202117807.Patil, R.S. et al. (2016), “Noria: A highly Xe-selective nanoporous organic solid”, Chemistry, Vol. 22, pp. 12618-12623, http://dx.doi.org/10.1002/chem.201602131.Soelberg, N.R., D. Banerjee, C. Simon, J. Atwood and P. Thallapally (2013), “Radioactive iodine and krypton control for nuclear fuel reprocessing facilities”, Science and Technology of Nuclear Installations, Vol. 2013, Article 702496, https://doi.org/10.1155/2013/702496.Yamawaki, M. et al. (2007), “Development of a Xenon recycling and supply system for plasma process”, International Symposium on Semiconductor Manufacturing: 1-4, http://dx.doi.org/10.1109/ISSM.2007.4446797.6. Platinum group metalsAs mentioned in Chapter 2, the intrinsic high value associated with the platinum group metals (PGM) makes them an obvious target for recovery, with the first three, ruthenium, rhodium, and palladium, being the ones that attract the most interest. From the earliest days of the nuclear sector, it has been speculated that the recovery of PGMs from spent nuclear fuel (SNF) might be worthy of consideration for commercial use and an assessment was made for the United States Atomic Energy Commission (United States Atomic Energy Commission, 1969). A review of the PGM market in 1970 (Newman and Smith, 1970) reached the following overall conclusions: “There are adequate mineral reserves under development and the recovery of fission products is not an imperative.The PGMs are recycled many times through the refineries and any radioactive contamination of this recycled pool would introduce irreversible hazards.The cost of recovering fission products and of decontaminating them (so far as may be possible) is likely to be high.The industrial demand has been for more platinum; in matching this demand there is more than adequate generation of the other PGMs.”However, circumstances change, and the topic has been revisited regularly, with a European study (Bourg and Poinssot, 2017) being one of the most recent. Bourg and Poinssot concluded that, with respect to PGMs, ruthenium and rhodium were the most viable while palladium is impractical since it cannot reach the threshold activity level of 100 Bq/g to be considered for free release. Specifically, Bourg et al. argued that, in the case of ruthenium, it could be possible to recover about 3.7 tonnes annually in France. This would represent about 20% of the world production and so would be possibly viable with a 2017 market price of 3-30 USD/g. Similarly, annual rhodium production from French reprocessed spent fuel could cover 3.5% of the 2014 world production and could be even more lucrative with a 2017 market price of USD 40-300/g. As of 19 January 2023, the Johnson Matthey base prices of Rh, Pd and Ru were (Johnson Matthey, 2023):Pd – 1 708.00 USD/troy ounce or 54.92 USD/g;Ru – 465.00 USD/troy ounce or 14.95 USD/g;Rh – 12 250.00 USD/troy ounce or 393.89 USD/g.Clearly, the amount of these materials present in the waste becomes irrelevant unless a practical way exists to separate these materials from the waste. This is the essential preliminary step prior to the purification of the individual PGM. As stated earlier, there has been a long-standing desire to recover PGMs from spent fuel; R.P. Bush stated that it would be difficult to achieve the necessary radiochemical separation by an oxidative distillation process and instead suggested that, by careful choice of conditions, solvent extraction, with a sulphur based extractant, might be used to separate rhodium and palladium from high-level liquid waste, but selectivity would be difficult to achieve (Bush, 1991). Bush concluded that the processes would tend to be relatively complex and expensive; so, at that time (1991), none of the processes could be regarded as economically viable candidates for industrial use. It is not clear whether Bush saw the processes as integral parts of a recycle regime or (more likely) additional processes treating nuclear waste that is already generated. For a future advanced recycle system, some of Bush’s concerns about shielding, etc. would be less valid since the PGM separation would not be an extra add-on facility but rather could be integrated into the design as part of a dedicated nuclear processing plant; however, the chemical complexities would remain. Clearly, since Bush undertook his review further developments have been made and (Bourg and Poinssot, 2017) noted that for ruthenium an efficient separation process could be based on the selective oxidation/volatilisation of Ru(VIII) followed by condensation at a lower temperature, which should achieve very high decontamination factors. That approach, along with other techniques, is discussed in a comprehensive review of ruthenium separation and recovery by Parveen K. Verma and Prasanta K. Mohapatra (Verma and Mohapatra, 2021).Before discussing the potential recovery routes for PGMs it is important to consider the potential radiological content of the recovered material. The typical isotopic composition of fission product PGMs in spent fuel is shown in Table 6.1. Table 6.1. Isotopic composition of fission product PGMs in spent fuelElementIsotopeContent (wt%)Half-lifeActivity (Bq)Ruthenium99TraceStable1004.2Stable10134.1Stable10234.0Stable103Trace39 days7.50E-1210423.9Stable1063.8368 days3.21E+13Rhodium102Trace2.9 years1.41E-02102mTrace207 days3.96E+11103100Stable106Trace30 seconds3.21E+13Palladium10416.9Stable10529.3Stable10621.3Stable10717.06.5 x 106 years8.36E+0910811.7Stable1103.8Stable Rh-106 exists in equilibrium with 106Ru and decays rapidly to 106Pd.As can be seen in Table 6.1, the presence of 107Pd means that any recovered palladium will be radioactive, so it might be mainly appropriate for other radiological applications, but the possibility of non-radiological applications should not be ruled out (see Section 6.1).For both ruthenium and rhodium, periods of decay storage would allow them to meet the free release threshold; 10 years of spent fuel cooling before recovery plus 25 years of interim storage (35 years in total) for ruthenium and a 50-year interim storage period would be needed before rhodium would meet the threshold activity level. Unlike France, where spent fuels are reprocessed after a short cooling period, these decay periods are consistent with the interim storage of spent fuel globally. It should be noted that France is one of the very few countries in the world that is reprocessing fuel. Currently, most SNF worldwide is being interim stored pending disposal or deployment of advanced fuel cycles. This means that these decay periods are not an issue for a country that is currently not reprocessing and provides stockpiles of long cooled fuels available for future reprocessing and recycling scenarios if the country changes its strategy for managing SNF.6.1. PalladiumPd recovery is commonly not recommended because it would not become free release (<100 Bq/g) in any reasonable length of time due to the long half-life of 107Pd (6.5 × 106 years). However, the presence of residual radioactivity need not be an insuperable barrier to industrial use in particular cases. Zdenek Kolarik and Edouard V. Renard noted the intrinsic radioactivity, as 107Pd is a soft beta emitter (maximum energy 0.035 MeV) with surface radiation intensity of only 520 Bq/cm2 and suggested that the recovered Pd could still be used in certain applications (Kolarik and Renard, 2005). The most obvious were applications in the nuclear industry, where the materials involved are themselves radioactive or become radioactive during operation. However, they also suggested other applications (such as in industrial catalysis) where the impact of the residual radioactivity could be satisfactorily controlled. (Kolarik and Renard, 2005) proposed the following general criteria for determining the suitability of a process for using recovered Pd:The cost of separating, processing, and using the recovered Pd should not exceed the costs of using naturally derived Pd.It must be possible to avoid irradiation and contamination of personnel and uncontrolled release of the radioactive Pd into the environment.It must be ensured that recycling of Pd, which frequently occurs in industry, does not result in the contamination of the general stock of the metals.The last point is especially important if there is any risk of introducing the recovered Pd into materials which later can be used in medicine or jewellery. Strict enforcement of common safety regulations for the treatment of radioactive materials should guarantee this – as they do currently for ex-source materials (e.g. 60Co) being excluded from general steel stocks. The criteria proposed by Zdenek Kolarik and Edouard V. Renard are equally applicable to other PGMs or indeed to reusing any material from the fuel cycle (Kolarik and Renard, 2005).Clearly, due to these extra restrictions, the economic value of radioactive Pd would be expected to be lower than that for non-radioactive Pd due to the limited number of applications in which it could be used. 6.2. Ruthenium Ruthenium has a complex chemistry that means that it can partition into a variety of process streams during waste management treatments, ranging from the acidic high-level liquid waste to alkaline low or intermediate-level liquid waste, or due to the volatile nature of its tetraoxide (RuO4) pass into the off-gas system and deposit in process pipes and stacks (Verma and Mohapatra, 2021).The volatility of the tetroxide, however, also makes it a promising recovery route for ruthenium because separation can be undertaken as part of off-gas abatement. Ruthenium can be driven into the off-gas system under oxidising or high-temperature processes and subsequently captured; this may be during traditional acidic fuel dissolution processes, or during high-level waste treatment, where elevated temperatures during calcination and vitrification can potentially release significant quantities of ruthenium. Volatile oxidised Ru species can be removed from off-gas waste streams by passing the off-gas through a scrubber. However, due to the low concentrations of volatile Ru in the off-gas, liquid scrubbers are not considered to be an effective technology for Ru capture. Solid adsorbers, such as silica gel, metal fibres/oxides or alloys were identified as better options for study in a recent review (Jubin et al., 2017). Subsequently, Spencer and Bruffey (2018) tested the effectiveness of 304 stainless steel wire cloth and Grade 0000 carbon steel wool and found estimated decontamination factors greater than 106 for sorbent beds composed of steel wool, although the penetration and amount of Ru sorbate varied strongly with the packing density of the steel wool. If the sorbent bed is sealed and delayed stored such that the 106Ru (half-life 372.6 days) has decayed to stable palladium to reach the free release threshold, the ruthenium could then be recovered. A recent review has been published on potential strategies for the recovery of ruthenium from spent nuclear fuel (Verma and Mohapatra, 2021): these authors considered strategies for both acidic and alkaline liquid streams.In acidic streams, many nitro, nitrate, and nitrosyl species are formed along with hydrolysed and polymeric species; this results in a low recovery percent of Ru and needs complex and/or innovative methods for improved separation. One of the easiest methods for the recovery of Ru from acidic feeds is by oxidation to RuO4 and subsequent back extraction using 2 mol/L sodium hydroxide solution containing 2% (vol%) sodium hypochlorite (Verma et al., 2018). Since chloro-based systems are less favoured (due to corrosion concerns), it is fortunate that aliphatic diluents such as n-hexane or n-dodecane can be used for trapping RuO4. However, the subsequent reduction to the black/brown RuO2⋅xH2O gives poor recovery results and is a major problem that depends on the kinetics of oxidation and subsequent trapping. Similarly, subsequent stripping kinetics are crucial and the eventual yield from acidic feeds is dependent on the effectiveness of the stripping agent and how fast it is done. In (Verma and Mohapatra, 2021), is reported that a membrane-based separation method has been shown to give >90% recovery but scaling up to process large volumes of feed solutions is expected to be challenging.Many intermediate-level liquid wastes are alkaline, so ruthenium recovery from alkaline systems is also important. Since anionic Ru species are present under alkaline conditions, appropriate ion exchanger systems would be attractive but, unfortunately, they are not very effective.The presence of higher salt contents in alkaline waste along with the presence of other anionic species such as AlO2- for example from the alkaline dissolution of aluminium clad fuel can interfere with the ion exchange process intended for ruthenium recovery with other anionic species exchanged with the anion exchange sites of the resin. However, in (Verma and Mohapatra, 2021), it is highlighted that the reductive property of the RuO4 to RuO2⋅xH2O, which is unique for Ru oxyanions that can occur at the resin surface, can overcome this problem. Since only Ru has this property of formation of oxides under reducing conditions (RuO2⋅xH2O) at the resin surface, other anionic species can be washed out, even if they exchange with the anion exchange resin using high concentrations of NaNO3. Photo-reduction has been suggested as one of the novel methods of Ru separation, as reported in a recent paper where simulated high-level liquid waste (HLLW) has been used (Li et al., 2017).6.3. RhodiumDuring reprocessing of SNF, Rh partitions to both the high-level waste (HLW) stream and the insoluble dissolver residue, and its recovery has been deemed strategically and economically favourable. Bourg and Poinssot (2017) compiled data of the key elements from the European critical list (published in 2014) that satisfied two conditions:The elements are present in SNF at concentrations greater than 1 ppm.The recoverable annual amount of the elements in French reprocessed spent fuel exceeds 0.1% of world production. Rhodium satisfies these requirements. In 2014, the total world production of Rh was 21 tonnes, while the potential French annual production of Rh from reprocessed SNF was 737 kg/year. Therefore, the amount of Rh that could be recovered annually from French spent fuel was equal to ~3.5% of the 2014 world production. For 50 GWd/tHM, 10-year cooled MOX fuel, ~5.6 kg of Rh per day is present in the HLW stream, corresponding to ~2 044 kg/year. The quantity of Rh in the HLW stream in 65 GWd/tHM, 10-year cooled uranium oxide (UOX) fuel, is slightly lower at ~3.7 kg/day, corresponding to ~1 350 kg/year. Therefore, the quantities of Rh present in the HLW stream after reprocessing are significant and recovery of the element would be highly valuable given the market price.6.3.1. Solvent extractionSolvent extraction is the main process used in nuclear fuel reprocessing. It offers many advantages as an industrial process:it is a safe, low-risk, mature technology;it is easily scalable and offers high selectivity;it enables achieving high product purity;it can operate at low-temperatures and pressures;the solvent and aqueous phases can be recycled and reused;it allows for high heavy metal loading capacity, which is important for PGM recovery (Kolarik and Renard, 2005).Solvent extraction of PGMs in a nitrate form is desirable, as nothing else needs to be added to the HLLW. Extraction as PGM nitrites would also be advantageous; however, the nitrous acid concentration in HLLW is not high enough to form extractable complexes. Adding further nitrous acid (or precursors) to HLLW is deemed acceptable as they can be easily destroyed when no longer required. Several studies have been published in which solvent extractions of Rh(III) (usually as the nitrate) are tested using a wide range of extractants and experimental conditions. The performance of the extractants is presented where possible in the terms of the distribution ratio for Rh (DRh), defined as the ratio of the total concentration of the extracted metal (in a particular valence state) in the organic phase to the corresponding total concentration remaining in the aqueous phase. In other cases, the extraction efficiency is expressed as the percentage of Rh(III) extracted into the organic phase from an initial amount of Rh(III) in the aqueous solution. This allows for comparisons to be made between the performance of each extractant.In earlier studies, extractants such as tributyl phosphate (TBP) in toluene, and trioctylphosphine oxide, Amberlite LA-1 and triisooctylamine in xylene, gave very poor Rh(III) extraction from 1-15 mol/L nitric acid. The phase contact time of two minutes employed in these studies is extremely short and even highlighted as “unfortunate” in the Zdenek Kolarik and Edouard V. Renard review (Kolarik and Renard, 2005). This is further explained by PGMs having a tendency for slow reaction kinetics in complex formation reactions. With such a short contact time, it is highly likely the reactions did not attain equilibrium. Later studies, therefore, carried out more comprehensive testing regimes, investigating factors such as the time taken to reach equilibrium, the effect of temperature, varying the concentration of the solution components (initial Rh(III), nitric acid, acidity and solution nitrate), and the addition of extraneous species to the system, i.e. salting-out reagents and the selectivity of the extraction for Rh(III) or PGMs. This led to some studies obtaining higher extraction values. Many of the extractants tested were only successful at higher temperatures, longer contact times, in lower concentrations of nitric acid (<1 mol/L) or solution nitrate ions, or in the presence of salting out agents. In conditions representative of the HLW raffinate stream, assuming 2-3 mol/L nitric acid concentration, the majority of extractants performed poorly. The good extraction performance of U and Pu in 2-3 mol/L nitric acid is utilised in the plutonium uranium reduction extraction (PUREX) process and so to minimise waste volumes it is important to maintain this acidity in the recovery of elements from PUREX high-level liquid waste. This also helps to control hydrogen production and avoid the formation of solids that can occur at lower acidities. In addition, as industrial solvent extraction processes are typically carried out with the aqueous and organic phases flowing in opposite directions (counter-current) through a series of contactors, the slow reaction kinetics may limit the viability of Rh(III) extraction in this type of large-scale process or batch processes may be more suitable. The best extraction performance found in the literature at conditions represented of the HLW raffinate stream was obtained using N, N', N''-tri-n-hexyl phosphorothioic-triamide(THPS) [(C6H13NH)3P=S] in heptanol, which gave a DRh value of ~50 in 2 mol/L nitric acid at 64°C in the presence of excess NaNO2, where the NO2-/Rh ratio was >20. This indicates almost quantitative extraction of the Rh(III) from the system (>98%). Without the addition of NaNO2, in 2 mol/L nitric acid at 64°C, 0.11 mol/L THPS attained good Rh(III) extraction with DRh = 3 in 8 hours (75%). However, full recovery may not be necessary and there may be a trade-off between processing costs (waste generated) versus the amount and value of material recovered.Aliquat 336 (10% v/v) in benzene extracted slightly over 60% Rh(III) at pzH 0.3 (~0.5 mol/L nitric acid concentration), reaching equilibrium in 1-10 minutes at 24°C. Although 0.5 mol/L nitric acid concentration was the highest tested, the extraction performance remained over 60% between pH 0.3 and pH ~6, so it would be of interest to test the extraction in higher concentrations of nitric acid. Extraction also increased with decreasing temperature, contrary to the trends seen in every other rhodium solvent extraction study found in the literature.Since about 2010, most of the research has concentrated on techniques like ionic liquid extraction, extractant loaded silica-polymer supports, and adsorption on functionalised silica materials.At the same time, there has been an apparent lack of reported studies that used conventional aqueous separation methods, except ion exchange, to specifically target Rh from HLLW raffinate/HNO3. Regarding commercially available ion exchange resins, a 2000-2004 series of Korean papers (Lee and Chung, 2000; Lee et al., 2004; Lee and Chung, 2003) are the most recent that explicitly target Rh.A similar situation exists with pyrochemical/molten salt/super high-temperature processes to target Rh from insoluble fission product residues, with little progress being reported since the 1990s (Naito et al., 1991; Uno et al., 1996).A recent review of the literature on the recovery of Rh from SNF (Hodgson et al., 2023), identified that Rh speciation in HNO3 was more complex than it appeared and has potentially been a bit underappreciated historically. It is now considered that the speciation of Rh in HNO3 solutions is influenced by many factors, including:the initial Rh complex dissolved in solution, i.e. [Rh(NO3)3]3+, [Rh(H2O)6]3+, RhCl3, etc;temperature, which increases ligand substitution rates;radioactivity, as radiolysis of HNO3 in HLLW raffinate can produce nitrite ions, NO2-, leading to the potential presence of a fraction of Rh nitrite complexes (Kolarik and Renard, 2003), such as [Rh(NO2)3(H2O)3] (Tatarchuk et al., 2003; Tatarchuk et al., 2006) or mixed-ligand Rh nitrate–nitrite complexes (Belyaev et al., 2002);equilibrium concentrations of [Rh, NO3-, H+] and other solution components.Now that this is a bit more understood, it might explain why all the newer papers focus on using processes that can be tailored towards specific targets. Examples would be researchers attaching various ligands to the cationic components of ionic liquids to make them more specific or combining multiple extractants and grafting them into porous silica supports.Taking these things together, it seems that the research community has moved away from conventional techniques, which have mostly reported poor recovery, and is trending towards more flexible and tuneable techniques. There still is not a single definitive method published for quantitative recovery but, with the current high price of Rh, even partial recovery might still be viable from an economic and strategic point of view.An interesting alternative approach is to use photo-reduction (Li et al., 2017). In this method, solutions are exposed to ultraviolet light or a laser with different wavelengths. Then, if reducing agents and photocatalysts are present, metal ions are photo-reduced to atoms that coalesce and grow to form metal particles. Experimental studies demonstrated the feasibility of the photochemical method for the efficient extraction and/or separation of Pd(II) and Ru(III) from lanthanides, which is beneficial for the potential recovery PGM as well as for the vitrification of the remaining HLLW.Figure 6.1. Illustration of photo-reduction for PGM recoverySource: NEA EGFRW data, 2023Note: Reproduced from (Li et al., 2017).6.4. ImPACTThe Japanese government-funded Impulsing PAradigm Change through disruptive Technologies (ImPACT) programme included a study from 2014 to 2018 entitled “Reduce and resource recycling of high-level radioactive waste through nuclear transmutation”. The aims of the programme were to develop transmutation pathways for long-lived fission products (LLFPs) such as 79Se, 93Zr, 107Pd and 135Cs to reduce the radiotoxicity of high-level waste and to develop opportunities for the reuse of valuable materials from spent fuels.Relevant to this report, the ImPACT programme aimed to recycle Pd and Zr after separation and transmutation processes for industrial use. For reuse, the safe level of contamination (or “clearance level”) was determined using life cycle and human exposure analyses. The specific isotopes of concern being 93Zr and 107Pd. Reuse of palladium in vehicle catalysts and dental prosthesis was considered with dental applications giving the highest potential dose. A limit of 10 µSv was applied equivalent to palladium with activity <3 300 Bq/g. For zirconium, reuse in nuclear power applications was envisaged and a clearance level of 90 Bq/g was determined.Separation processes from simulated high-level liquid waste were, therefore, tested, including potentiostatic electrolysis for palladium (recovery of 95%) and extraction with N, N-didodecyl-2-hydroxyacetoamide for zirconium (recovery of 90%). Additionally, recovery of LLFPs from vitrified high-level waste was investigated using both wet (acidic leaching) and dry (molten salt electrolysis) chemical processes. Zirconium recovery from zirconium molybdates, insoluble precipitates that are formed in reprocessing, was investigated via fluorination. Another innovative technology investigated was the selective laser ionisation of odd-mass isotopes to transmute the radioactive isotopes of palladium (107Pd) and zirconium (93Zr) from chemically separated solutions. Separation factors up to 1 000 were obtained for Pd.6.5. ReferencesBelyaev, A.V. et al. (2002), “State of radiorhodium in high-level liquid waste from regeneration of spent nuclear fuel”, Radiochemistry, Vol. 44, pp. 546–558, http://dx.doi.org/10.1023/A:1022324208620.Bourg, S. and C. Poinssot (2017), “Could spent fuel be considered as a non-conventional mine of critical raw materials?”, Progress in Nuclear Energy, Vol. 94, pp. 222-228, https://doi.org/10.1016/j.pnucene.2016.08.004.Bush, R.P. (1991), “Recovery of platinum group metals from high level radioactive waste: possibilities of separation and use re-evaluated”, Platinum Metals Review, Vol. 35 (4), pp. 202-208, https://doi.org/10.1595/003214091X354202208.Hodgson, B.J., J.R. Turner and A.F. Holdsworth (2023), “A review of opportunities and methods for recovery of rhodium from spent nuclear fuel during reprocessing”, J. Nucl. Eng., Vol. 4, pp. 484-534, https://doi.org/10.3390/jne4030034.Johnson, M. (2023), PGM management [Online], available: https://matthey.com/products-and-markets/pgms-and-circularity/pgm-management (Accessed: 19 Jan. 2023).Jubin, R.T., S.H. Bruffey, B.B. Spencer and D.M. Strachan (2017), Evaluation of Ruthenium Capture Methods for Tritium Pretreatment Off-Gas Streams, ORNL/TM-2017/330, NTRD-MRWFD-2017-000312, Oak Ridge National Laboratory, United States.Kolarik, Z. and E.V. Renard (2003), “Recovery of value fission platinoids from spent nuclear fuel Part I: General considerations and basic chemistry”, Plat. Met. Rev., Vol. 47, pp. 74-87, https://doi.org/10.1595/003214003X4727487.Kolarik, Z. and E.V. Renard (2005), “Potential applications of fission platinoids in industry”, Platinum Metals Review, Vol. 49, pp. 79-90, https://doi.org/10.1595/147106705X35263.Lee, S.H. and Chung, H. (2000), “Ion exchange characteristics of palladium and rhodium from a simulated radioactive liquid waste”, J. Nucl. Sci. Tech., Vol. 37, pp. 281-287, https://doi.org/10.1080/18811248.2000.9714895.Lee, S.H., J.H. Yoo and J.H. Kim (2004), “Ion exchange characteristics of rhodium and ruthenium from a simulated radioactive liquid waste”, Kor. J. Chem. Eng., Vol. 21, pp. 1038-1043, http://dx.doi.org/10.1007/BF02705590.Lee, S.H. and H. Chung (2003), “Ion exchange characteristics of palladium and ruthenium from a simulated radioactive liquid waste”, Sep. Sci. Tech., Vol. 38, pp. 3459-3472, HYPERLINK "https://doi.org/10.1081/SS-120023411"https://doi.org/10.1081/SS-120023411.Li, F. et al. (2017). “Efficient extraction and separation of palladium (Pd) and ruthenium (Ru) from simulated HLLW by photoreduction”, Separation and Purification Technology, Vol. 182, pp. 9-18, https://doi.org/10.1016/j.seppur.2017.03.029.Naito, K. et al. (1991), “Recovery and mutual separation of noble metals from the simulated insoluble residue of spent fuel”, J. Nucl. Mater., Vol. 184, pp. 30-38, https://doi.org/10.1016/0022-3115(91)90529-G.Uno, M., Y. Kadotani, H. Kinoshita and C. Miyaki (1996), “Processing high-level liquid waste by super-high-temperature method, (IV): Reducing reactions and alloy formation by platinum group elements, molybdenum and corrosion products taking place in simulated HLLW”, J. Nucl. Sci. Tech., Vol. 33, pp. 973-980, https://doi.org/10.1080/18811248.1996.9732040.Newman, R.J. and F.J. Smith (1970), “Platinum metals from nuclear fission: An evaluation of their possible use by industry”, Platinum Metals Review, Vol. 14(3), pp. 88-92, https://doi.org/10.1595/003214070X1438892.Spencer, B.B. and S.H. Bruffey (2018), Initial Series of Ruthenium Adsorption Optimization Studies, ORNL/SPR-2018/913, NTRD-MRWFD-2018-000197, Oak Ridge National Laboratory, United States.Tatarchuk, V.V., T.M. Korda, A.N. Tatarchuk and V.G. Torgov (2003), “Solvent extraction of differently charged aquanitro forms of rhodium (III) with reference to the recovery of the fission rhodium from nitrate-nitrite solutions”, Chem. Sust. Dev., Vol. 11, pp. 755-764.Tatarchuk, V.V., I.A. Druzhinina, T.M. Korda and A.N. Tatarchuk (2006), “Kinetics of rhodium extraction from nitric acid solutions with a mixture of dihexyl sulfide and alkylanilinium nitrate”, Russ. J. Inorg. Chem., Vol. 51, pp. 1977-1987, https://doi.org/10.1134/S0036023606120229.United States Atomic Energy Commission (1969), “USAEC Report BNWL-1010”, Battelle Memorial Institute, Pacific Northwest Laboratories.Verma, P.K and P.K Mohapatra (2021), “Ruthenium speciation in radioactive wastes and state-of-the-art strategies for its recovery: A review”, Separation and Purification Technology, Vol. 275, https://doi.org/10.1016/j.seppur.2021.119148.Verma, P.K., R.B. Gujar and P.K. Mohapatra (2018), “An efficient method for radio-ruthenium separation from acidic feeds: Extraction, transport and spectroscopic studies”, Journal of Environmental Chemical Engineering, Vol. 6, Issue 5, pp. 5830-5836, https://doi.org/10.1016/j.jece.2018.08.062.7. Rare earth elementsThe highest-concentration fission products (FPs) by elemental class are the rare earth elements (REEs) (Holdsworth et al., 2021), covering the elements Y, La, Ce, Pr, Nd, Pm, Sm, Eu, Gd, and Tb. Of these, Pr, Nd, and Gd are the most valuable (~USD 117/kg for Pr2O3 and Nd2O3, and USD 41/kg for Gd2O3) (SMM, n.d.). These versatile elements find a wide array of uses across modern, advanced technologies including clean energy (Natrajan and Langford Paden, 2013).The REEs i.e. lanthanides, yttrium and scandium are often cited as a critical resource. This is due to China’s overall control of the market, from mining to the end-metal products, resulting in full industrial dependency in many countries, including in Europe and North America. Alternative measures to source these materials are of critical importance as currently 41% of worldwide consumption is due to newer, high-growth markets (Charalampides et al., 2015) that will accelerate the demand for this resource. There is also an environmental consideration for reducing production of REEs by mining as ores in which these elements are found often contain thorium and uranium, generating additional radioactive waste as well as toxic heavy metal containing waste (Fernandez, 2017). Serious environmental impacts of REE mining have been reported (Balaram, 2019).As a result, to minimise new mining many countries have considered extraction of REEs from waste streams including aqueous solutions as well as sludges. In the United States, West Virginia University was awarded USD 5 million to research methods for retrieval of REEs from acid mine drainage (Kruger, 2019). Their research primarily focuses on retrieval from sludge media. REE recovery from electronic wastes is also an area of growing interest (Tunsu et al., 2015; Natrajan and Langford Paden, 2013). The US DOE has explored retrieval of rare earth fission product from powdered spent nuclear fuel. For example, the patent (Christian, 2016) proposed the generation of a mixture using Zr or Th, heating of the mixture and subsequent extraction of rare earth elements from the mixture.When considering how to extract REEs from spent nuclear fuel (SNF), it is worth noting that most of the proposed minor actinide (MA) separation and recovery processes also partition and separately strip the chemically similar REEs (Natrajan and Langford Paden, 2013), thus providing a viable recovery route to these elements. For example, Stéphane Bourg and Christophe Poinssot proposed a recovery of the REE from spent fuel dissolution liquors after a plutonium uranium reduction extraction (PUREX) process (Bourg and Poinssot, 2017) as implemented at the Orano La Hague Plant, coupled with the diamide extraction – selective actinide extraction (DIAMEX-SANEX) processes (Lecomte, 2008) to allow the separation and the recovery of REE from PUREX raffinate. However, they would need to be separated one from each other, thus an additional step would be required, based on existing processes, such as the ones implemented today at Solvay’s Plant at La Rochelle (France). Similarly, in their review of which strategic materials could be recovered form SNF Alistair F. Holdsworth and colleagues) noted that following the MA extraction the subsequent separation of the individual REEs from each other can be achieved using conventional, industrial chromatographic techniques (Holdsworth et al., 2023, Asadollahzadeh et al., 2020; Chen et al., 2022; Opare et al., 2021). However, while chemical separation methods are available, the extent that recovered materials can be used in non-nuclear applications will depend primarily on the activity of the radioisotopes present, although some applications may be able to tolerate higher residual activities. Bourg and Poinssot considered the implications of having an interim decay storage period and highlighted that against a release threshold value of 100 Bq/g, Nd, Pr and Gd could be recycled in non-nuclear industry after about 10 years of interim storage and Ce after 20 years, but the activity of Eu, Sm and Pd remains too high to be reused whatever the interim storage time (Bourg and Poinssot, 2017). Consequently, the better options may be to capitalise on the most commercially valuable REEs such as Pr, Nd, and Gd, which exist only as stable isotopes, alongside Y, La, and Tb. Ce, Sm, Pm and Eu all have radioisotopes, meaning effective separation with low levels of contamination between elements will be needed, coupled with a decay storage regime.7.1. Recovery of lanthanidesHistorically, the lanthanides have been separated from one another using fractional crystallisation techniques, originally developed by Charles James in the early 20th century, which enabled chemists to separate large amounts of ytterbia into ytterbium and lutetium using bromates and magnesium nitrates (James, 1907). The separation regime is illustrated in Figure 7.1.Figure 7.1. Lanthanide separation from the minerals cerite and ytterbiteusing fractional crystallisation techniquesSource: NEA EGFRW data, 2023.The “James method” relies on the regular decrease in the ionic radii across the lanthanide series from La3+ to Lu3+. As the lanthanide series is traversed, their salts become slightly less ionic, which leads to small changes in their chemical properties (e.g. Ce(OH)3 is more basic than Yb(OH)3 and Lu(OH)3). The aqueous ions become more acidic and the enthalpy of hydration and complexation (with ligands) increases. Nevertheless, the similar ionic radius and persistence of the +III oxidation state renders chemical separation of the 4f elements rather challenging. The advent of ion exchange chromatography in the 1940s enabled much larger quantities of the rare earths to be separated and refined using cation exchange resins such as Dowex (Choppin and Dinius, 1962). The rare earth ions are eluted in accordance with their relative atomic weight and size, where the lighter members of the series are eluted before the heavier elements, which possess a smaller hydrated ionic radius. This separation can be enhanced using extractants such as citric acid or citrates by using ethylenediaminetetraacetic acid (EDTA) as the eluting agent or lactates, hydroxybutyrate and a-hydroxycarboxylates, facilitating the isolation of kilogram quantities of pure rare earth ions for use in commercial products.TALSPEAK processIn the early 1960s, the Oak Ridge National Laboratory (ORNL) in Tennessee, United States, developed the Trivalent Actinide Lanthanide Separation by Phosphorus reagent Extraction from Aqueous Complexation (TALSPEAK) (Weaver and Kappelmann, 1964), which is an effective method of advanced reprocessing by solvent extraction. The process is designed to allow the separation of MA3+ (Am3+ and Cm3+) from Ln3+ and Y3+ to allow MA3+ to be reprocessed further; the separation of americium is discussed in detail in Section 3.2.The TALSPEAK process uses di(2-ethylhexyl) phosphoric acid (HDEHP), or similar liquid cation exchanger to extract lanthanides from a medium that selectively retains the actinides in the aqueous phase as complexes with polyaminopolyacetic acid complexants. In the original process, (Weaver and Kappelmann, 1964) used diethylene triamine-N,N,N’,N”,N”-pentaacetic acid (DTPA) and lactic acid (LA) in the aqueous phase.The process relies on the extraction mechanism for HDEHP in acidic nitrate media being able to change from a chelating (ion exchange) mechanism to a solvating mechanism as the nitrate concentration increases (Svantesson et al., 1980). The overall process is summarised in following two chemical steps:conditioning of aqueous feed solution with DTPA and lactic acid (LA):M(NO3)3 + H5DTPA ↔ M(NO3)3-n H5-nDTPA + n(NO3);H+ + LA- ↔ HLA (Buffer action to control pH);biphasic reaction between poorly bonded DTPA-metal ions and HDEHP;M(NO3)3-n H5-nDTPA + 3(HDEHP)2 ↔ M(DEHP·HDEHP)3 + H5DTPA + (3-n)H+ + (3-n)NO3.Note that the underlined species are present in the organic phase.In the above reactions, the DTPA acts as an actinide complexing reagent that keeps the actinides in the aqueous phase, while the HDEHP is the lanthanide extractant. The lanthanides are then extracted into diisopropylbenzene (DIPB) containing HDEHP. This separation process is based upon the competition between HDEHP in the extracting phase and lactate buffered DTPA in the aqueous phase.Under ideal conditions, the TALSPEAK process (as described above) separates Am3+ from Nd3+ (the usual limiting pair) with a single-stage separation factor of about 100; both lighter and heavier lanthanides are more completely separated from Am3+ with the order of extraction of trivalent lanthanides and Am3+ being (Nilsson and Nash, 2007):Am << Nd < Pm < Sm = Eu < Pr < Ce = Gd < La < Tb < Dy < Ho < Er < Tm < Yb < LuThe original TALSPEAK flowsheet for purification of americium and curium is shown schematically in Figure 7.2 below.Figure 7.2. Original TALSPEAK flowsheet for purification of americium and curiumSource: NEA EGFRW data, 2023.Note: Reproduced from (Weaver and Kappelmann, 1964).With several decades of research to underpin it, the TALSPEAK process has become a widely recognised benchmark for advanced aqueous partitioning of the trivalent 4f/5f elements and it has also been used as an actinide-selective stripping agent (so-called Reverse TALSPEAK) with some notable success (Nilsson and Nash, 2007). While much of the underpinning research and development has focused on determining the kinetics, thermodynamics and speciation along with process optimisation, consideration has also been given to using alternative reagents, so-called “Advanced TALSPEAK” for example, using the preferential binding of the actinides in the aqueous phase by N-(2-hydroxyethyl)ethylenediamine-N, N’, N’-triacetic acid (HEDTA), which serves to keep the actinides in the aqueous phase while the lanthanides are extracted into an organic phase containing 2-ethylhexylphosphonic acid mono-2-ethylhexyl ester (HEH[EHP]) (Lumetta et al., 2015; Wilden et al., 2017). Another interesting adaption of the TALSPEAK process is to apply it on hollow fibre renewable liquid membrane (HFRLM) (Kedri et al., 2020). So, while the TALSPEAK process is primarily designed for MA recovery, it also produces a REE-rich waste stream that could be used. A characteristic of TALSPEAK is its versatility, with different combinations of extractant, aqueous complexing agent, buffer solution, pH value, and temperature being able to deliver different separation effects for REEs as shown by Xiaoqi Sun and colleagues (Sun et al., 2014), who used functionalised ionic liquids in a TALSPEAK-like process. Despite such developments, challenges remain in the development of lanthanide/actinide separation processes that are salt-free in aqueous and organic phases (i.e. that follow the carbon, hydrogen, oxygen, and nitrogen atoms “[CHON] Principle”, where ligands are only comprised of carbon, hydrogen, oxygen and nitrogen atoms) and operate in the acidic (>0.1 mol/L HNO3) rather than high pH region for the difficult Ln/An separation stage. This is a major drawback of processes such as TALSPEAK, which require stripping at high pH and within a rather narrow pH window and are thus difficult to operate at the engineering scale. Consequently, other approaches have been developed that try to address this, such as innovative selective actinide extraction (i-SANEX), which would be used alongside an advanced plutonium uranium extraction (PUREX), or the alternative approach of grouped actinide extraction (GANEX). These are described in the next section.GANEX and i-SANEX processesGrouped actinide extraction (GANEX) was initially developed by the CEA (France) for recovery of all the transuranic actinides together. This was to support the scenario of homogeneous recycling of actinides (including the minor actinides) in fast reactors (Lyseid Authen et al., 2022). The CEA proposed a two-stage approach in which an initial solvent extraction cycle recovers the bulk uranium from the transuranic actinides and fission products. This simplifies the chemistry of the second stage and reduces the volumetric flows (and hence size of plant) needed for the more complicated recovery of all the transuranium (TRU) actinides from the fission products. The CEA tested the extractant GANEX first cycle (GANEX-1) in their hot cells at the ATALANTE facility (Modolo et al., 2015). It was based on an extraction with the mono-amide ligand N,N-di-(ethyl-2-hexyl)isobutyramide (DEHiBA), which is selective for uranium(VI) ions over plutonium(IV) and other metals. DEHiBA conforms to the CHON principle and has relatively fast extraction kinetics and good radiolytic stability making it a suitable option for this stage. The European Joint Research Centre (JRC, Karlsruhe) also later tested the GANEX-1 cycle in their hot cells but with fast reactor fuels (higher plutonium content) and with short residence time centrifugal contactors in place of mixer-settlers (used in the CEA test) (Malmbeck et al., 2019). Both tests gave promising results although some optimisation, particularly with respect to technetium decontamination, was still required (technetium partly co-extracts with the uranium).The second cycle of the overall GANEX process (GANEX-2) focuses on the recovery of all the TRU actinides (Np-Cm) as a group. The grouped recovery is preferred since this is conceptually simpler and adds some enhanced proliferation barriers to the plutonium-containing product although it complicates downstream fuel fabrications, so separated recoveries of Pu+Np and Am+Cm have also been considered (Carrott et al., 2016). Three options have so far been proposed for this stage. Initially, the CEA used a variation on their DIAMEX-SANEX process (which is similar to the reverse TALSPEAK process) with the combination of N,N’-dimethyl-N,N’-dioctyl-2-(2-hexyloxyethyl)-malonamide (DMDOHEMA) and HDEHP in the organic phase and HEDTA, citric acid and hydroxyurea in the aqueous phase to selectively strip the actinides at pH 3. The lanthanides, together with iron and zirconium were retained in the organic phase and were subsequently stripped back into the aqueous phase (Modolo et al., 2015).An improvement to the CEA-GANEX cycle was developed under European collaborative projects (Lyseid Authen et al., 2022) and tested in the JRC hot cells using the raffinate from their GANEX-1 hot test, i.e. derived from fast reactor fuels with high plutonium contents (Malmbeck et al., 2019). This used N,N,N',N’-tetraoctyl diglycolamide (TODGA) with DMDOHEMA in the organic phase and a combination of acetohydroxamic acid (AHA) and a (SO3-Ph-BTP) in the aqueous phase. The main advantage was the ability to operate the flowsheet in the sulphonated bis-triazinyl pyridine acidic rather than pH range (>0.1 mol/L nitric acid) together with the capacity to handle high plutonium concentrations in the organic phase. Very good recoveries of the actinides were obtained with low contamination from fission products, including the chemically similar lanthanides. Again, this option (termed EURO-GANEX) is based on a reverse-TALSPEAK-like coextraction of actinides and lanthanides followed by selective stripping of the actinides. The lanthanides are then separately backwashed into the aqueous phase.The third option proposed for the GANEX-2 cycle is the so-called chalmers extraction (CHALMEX) process (Lyseid Authen et al., 2022). This, however, is based on selective extraction of the actinides directly from the GANEX-1 aqueous raffinate. Therefore, regarding the aims of this report, both the CEA-GANEX and EURO-GANEX present greater opportunities to recover REE from the lanthanide-rich final aqueous waste stream (which has been purified from most of the fission product and actinide elements). In the development of options for future reprocessing of spent fuels these opportunities should be evaluated in the design stage. The EURO-GANEX cycle is illustrated in Figure 7.3.Figure 7.3. Schematic of the EURO-GANEX cycleSource: NEA EGFRW data, 2023.Note: Reproduced from (Malmbeck et al., 2019).The innovative i-SANEX process presents similar opportunities to the CEA and EURO-GANEX processes just mentioned. Briefly, this is designed as an “add-on” to the PUREX process for the recovery of the MA from the highly active raffinate to enable the heterogeneous recycling of the MA in advanced reactors (Geist et al., 2020). It also uses TODGA in the organic phase with octanol as a phase modifier and the SO3-Ph-BTP molecule in the aqueous phase (i.e. it employs co-extraction of actinides and lanthanides followed by selective stripping of MA) and has been tested in centrifugal contactors (Modolo et al., 2015). As with the GANEX processes, a lanthanide-rich aqueous waste stream is obtained from which REE could be recovered if desired.7.1.1. Promethium-147 recovery in the United StatesIn the past, high-purity promethium-147 (147Pm) was recovered in up to M Ci-per-year amounts for use in beta energy voltaic applications. This was, however, in the 1960s and 1970s, when large amounts of irradiated fissile uranium were available from US government operations at Idaho Chemical Processing Plant, the Hanford Site, and the Savannah River Site (SRS). Moreover, the irradiated uranium feedstock was available after relatively short decay periods following reactor discharge. Shorter decay time is a major factor since the half-life of 147Pm is 2.62 years.Recovery of small amounts of high purity 147Pm, up to 1 K Ci per year, has been resumed at Oak Ridge National Laboratory (ORNL) to supply domestic customers. In consideration of the recovery of 147Pm now and in the future, it is pertinent to review the historical production and evolution of separations technology.Separations of irradiated uranium from the Graphite Reactor began at ORNL in 1947 using ion exchange methods (Pressly et al., 1960). Separation of 147Pm for sale began in 1950. As the demand for this isotope increased through the 1950s, the amount recovered and purified per year increased from 11 mCi/yr to 53 Ci/yr by 1956. In 1958, a much larger source of rare earth elements in fission product waste was obtained from the Idaho Chemical Processing Plant, enabling recovery and purification to increase to 830 Ci/yr. Solvent extraction was used to recover the rare earth elements and yttrium from aluminium nitrate waste solution, followed by iodate precipitation to remove the cerium. Final purification of 147Pm was done by ion exchange.Production increased again in 1959 by a factor of 20, to ~18 000 Ci, using solvent extraction methods to recover and remove yttrium and cerium (primarily, the high gamma emission from 144Ce/144Pr) and produce a “crude” rare earth product for subsequent purification. This work was done in ORNL’s Fission Products Pilot Plant, later known as the Fission Products Development Laboratory. Portions of the crude rare earth product were transferred to a shielded hot cell facility (Building 3028 in the Isotopes Circle area) containing four large-scale ion exchange columns (each 8 ft long, three with 3 in. diameter, and one with 2 in. diameter) to separate kilocurie amounts of 147Pm from the other rare earth fission products by means of cation exchange chromatography using ammonium citrate at pH 3.0 as the complexing eluent. Thereafter, the Pm product was converted to an oxide form suitable for source fabrication. Product specifications were >450 Ci of 147Pm per gram of total rare earth oxide and <3 microcuries of gamma contamination per Ci of 147Pm. Typical product had a chemical purity of ~65%.Production and process improvement continued at ORNL into the early 1960s. Orr (Orr, 1962) showed that by using diethylene triamine pentaacetic acid (DTPA) at pH 5 and a temperature of 70°C-80°C , the order of elution of the elements from cation exchange resin (80 mesh Dowex 50W-X4) was changed, from that obtained with citrate where americium (Am) and Pm were eluted together to a Pm product containing no detectable Am.Also in the early 1960s, Wheelwright and Roberts, at Battelle Northwest Laboratory (BNWL) (now Pacific Northwest National Laboratory [PNNL]), developed a large-scale method of displacement cation exchange chromatography (Wheelwright and Roberts, 1963) from previous tracer-level work at Ames Laboratory. The displacement ion was initially Cu (II), but it was later found to be susceptible to reaction with the complexing eluent (ethylenediaminetetraacetic acid [EDTA]) and was replaced by Zn (II) in subsequent operations. Wheelwright and colleagues (Wheelwright et al., 1966) studied the processes used by commercial natural rare earth separators and evaluated the elution parameters, as well as the complexing eluents, EDTA, DTPA, and hydroxyethylethylenediaminetriacetic acid, which had all been used successfully for purification of Pm and other individual “light” rare earth elements on a macroscale. DTPA was demonstrated to be superior. Optimised operating conditions allowed a fourfold reduction of both the elution time cycle and the volume of waste solution generated.A two-stage purification process was set up at Hanford in the mid-1960s. The first stage involved recovery of crude Pm from the uranium–plutonium reprocessing raffinates in large-scale solvent extraction operations, likely using di-2-ethylhexyl phosphoric acid (HDEHP) as the extractant. In some cases, the high gamma-emitting cerium radioisotopes were removed from the crude Pm at the reprocessing site by oxidising Ce (III) to Ce (IV) and then preferentially extracting the Ce (IV) using HDEHP at high acidity (Wheelwright et al., 1966).The second stage involved Pm purification that was based on the process and equipment development and demonstration of Wheelwright and colleagues (Wheelwright et al., 1966). A large-scale cation exchange chromatography purification system was installed in one of the hot cells at BNWL (now PNNL, Building 325). Seven gravity-fed, 9-ft-high columns ranging in diameter from 8 in. to 1 in. were used. From October 1965 to October 1966, a total of ~1 MCi of 147Pm was purified in 11 batch runs ranging in size from 63 to 145 KCi. The chemical purity of the Pm averaged 98%-99%. The major impurities were neodymium (Nd) and samarium, each at an average composition of <1%.The equipment at BNWL was operated 24 hours per day, 5 days per week by a team of 7 to 8 people (2 technicians per 8-hour shift, plus a support technician per day and a chemist as needed).Production at the SRS was briefly demonstrated in 1970 (Lowe, 1969), (Lowe, 1970), (Greene, 1971). Almost 3 MCi of 147Pm, in the form of crude Pm, was produced in the SRS reactors and recovered in the F-Canyon reprocessing plant. Improvements of the displacement chromatography purification process were developed at the Savannah River Laboratory (SRL) and demonstrated in one ~1 KCi test. The improved features included the use of a narrow range of small resin size (i.e. 30 to 60 microns) to enable a sharper separation of the rare earth elements and americium impurities from promethium. Alternatively, equivalent peak separation at higher flow rates could be done, which decreases exposure time and damage due to high activity levels. The equipment used, operating conditions and product analysis results for the SRL demonstration are described in (Lowe, 1969). Briefly, three 5-ft-long columns were filled with 400 mesh Dowex 50- X8 resin and loaded with the Zn barrier ion, followed by the crude Pm feed. The three columns had successively smaller diameters to enable improved separation of the component elution bands. All columns were operated at 70oC to move the bands rapidly through the columns and minimise radiation damage to the resin. Valve placement enabled initial flow only through the first column. When the leading edge of the elution band neared the bottom of the first column, the flow rate was lowered to maintain the same flow velocity in the second column, which was then opened to flow. A similar procedure was used for flow through the third column. Effluent fractions from the third column were collected in 500 mL fractions. Analytical results showed that 99.89% of the Pm activity was collected in one fraction and that radioactive isotope impurities were separated by factors of 1.7E3 to >6.4E3.Earlier in the 1960s, while product demand was growing and the production operation was ramping up, several studies were conducted at BNWL and the General Electric Company Hanford Atomic Products Operation (i.e. the Hanford Site) to (1) provide an engineering study for a Hanford Isotopes Production Plant (LaRivierre et al., 1963), (2) appraise the magnitude and values in spent fuel from power reactors (Rohrmann, 1965), and (3) evaluate the prospects for large-scale production of Pm (McKee, 1966). The third study (McKee, 1966) reviewed the potential requirements for 147Pm as a heat source isotope and compared these requirements with the estimated availability of fission product 147Pm, both from a proposed private initiative by a commercial company to process Hanford reactor spent fuel and from future power reactor spent fuel reprocessing. Additionally, the economic feasibility of producing additional 147Pm by irradiation of enriched neodymium-146 (146Nd) was evaluated and found to be unattractive because it requires an expensive feedstock inventory. The conversion to 147Pm had to be limited because the neutron cross-section for 146Nd (i.e. the feedstock) was smaller than that for the product, 147Pm; thus, the product can be destroyed faster than it is produced.By 1974, the accumulated inventory at BNWL included 6.5 MCi of crude Pm and 1.8 MCi of purified product (USAEC, 1974). However, the market for 147Pm had begun to decline. A decision was made to forego further production of crude Pm and sell out the inventory to smaller users. Thus, the last of the inventory of crude Pm was purified in September 1980 at BNWL, and 215 KCi was sent to ORNL for distribution. The distribution was continued until 1989 when ORNL facilities were shut down and the 147Pm had mostly decayed.The potential for production and purification of 147Pm and other fission product isotopes was examined in the mid-1960s for a full-scale reprocessing plant and was found to be substantial, in the range of tens of MCi per year. At that time, the use of power reactors was just beginning. Even with the spent fuel burn-up level expected then (~25 GWd/t), the potential yields were large. Today, routine spent fuel burn-up levels are in the range of 50 to 60 GWd/t, so even greater yields could be possible.The high-performance liquid chromatographic method of separating adjacent actinide elements has been applied successfully to heavy actinides at ORNL and SRL since the 1970s. The process (Benker et al., 1981) is cation exchange chromatographic elution with ammonium alpha-hydroxy-isobutyrate at various pH levels. The zinc displacement method was applied successfully at SRL (Lowe et al., 1971) to separate kilogram amounts of adjacent actinides, using DTPA as the eluent. The separation of either adjacent actinide or lanthanide elements can be applied successfully because the actinides and lanthanides are chemically similar and the difficulty in separating adjacent elements is similar (Campbell, 1981).7.2. ReferencesAsadollahzadeh, M., R. Torkaman and M. Torab-Mostaedi (2020), “Extraction and separation of rare earth elements by adsorption approaches: Current status and future trends”, Sep. Purif. Rev. 2020, Vol. 50, pp. 417-444, https://doi.org/10.1080/15422119.2020.1792930.Balaram, V. (2019), “Rare earth elements: A review of applications, occurrence, exploration, analysis, recycling, and environmental impact”, Geoscience Frontiers, Vol. 10, pp. 1285-1303, https://doi.org/10.1016/j.gsf.2018.12.005. Benker, D.E. et al. (1981), “Chromatographic cation exchange separations of decigram quantities of californium and other Transplutonium elements”, Transplutonium Elements–Production and Recovery, ACS Symposium Series No. 161.Bourg, S. and C. Poinssot (2017), “Could spent fuel be considered as a non-conventional mine of critical raw materials?”, Progress in Nuclear Energy, Vol. 94, pp. 222-228, https://doi.org/10.1016/j.pnucene.2016.08.004.Campbell, D.O. (1981), “The application of pressurized ion exchange to separations of transplutonium elements”, Transplutonium Elements–Production and Recovery, ACS Symposium Series no. 161.Charalampides, G. et al. (2015), “Rare earth elements: Industrial applications and economic dependency of Europe”, Procedia Economics and Finance, Vol. 24, pp. 126-135, https://doi.org/10.1016/S2212-5671(15)00630-9.Chen, Z. et al. (2022), “Recent advances in selective separation technologies of rare earth elements: A review”, J. Environ. Chem. Eng, Vol. 10, https://doi.org/10.1016/j.jece.2021.107104.Christian, J.D. (2016), “Separation of the rare-earth fission product poisons from spent nuclear fuel”, Idaho Falls, https://image-ppubs.uspto.gov/dirsearch-public/print/downloadPdf/9428401.Choppin, G.R. and R.H. Dinius (1962), “Ion-exchange studies of the lanthanides and actinides in concentrated mineral acids”, Inorg. Chem., Vol. 1, 140, HYPERLINK "https://doi.org/10.1021/ic50001a027"https://doi.org/10.1021/ic50001a027.Carrott, M. et al. (2016), “TRU-SANEX”: A variation on the EURO-GANEX and i-SANEX processes for heterogeneous recycling of actinides Np-Cm”, Separation Science and Technology, Vol. 51(13), pp. 2198-2213, https://doi.org/10.1080/01496395.2016.1202979.Fernandez, V. (2017), “Rare-earth elements market: A historical and financial perspective”, Resources Policy, Vol. 53, pp. 26-45, https://doi.org/10.1016/j.resourpol.2017.05.010.Geist, A. et al. (2020), “An overview of solvent extraction processes developed in Europe for advanced nuclear fuel recycling, part 1 – heterogeneous recycling”, Separation Science and Technology, Vol. 56, pp. 1866-1881, https://doi.org/10.1080/01496395.2020.1795680.Greene, R.E. (1971), “Recovery of 147Pm from Savannah River Plant Waste”, Isotopes and Radiation Technology, Vol. 9(1).Holdsworth, A.F., H. Eccles, C.A. Sharrad and K. George (2023), “Spent nuclear fuel – waste or resource? The potential of strategic materials recovery during recycle for sustainability and advanced waste management”, Waste, Vol. 1(1), pp. 249-263; https://doi.org/10.3390/waste1010016.Holdsworth, A.F., K. George, S.J. Adams and C.A. Sharrad (2021), “An accessible statistical regression approach for the estimation of spent nuclear fuel compositions and decay heats to support the development of nuclear fuel management strategies”, Prog. Nucl. Energy, Vol. 141, 103935, https://doi.org/10.1016/j.pnucene.2021.103935.James, C. (1907), “A new method for the separation of the yttrium earths”, J. Am. Chem. Soc., 1907, Vol. 29, 495, https://doi.org/10.1021/ja01958a010.Kedri, C.S., J.S. Yadav and C.P. Kaushik (2020), “TALSPEAK process on hollow fiber renewable liquid membrane apropos to the remedial maneuver of high-level nuclear waste”, Journal of Hazardous Materials, https://doi.org/10.1016/j.jhazmat.2020.123050.Kruger, M. (2019), WVUToday website, West Virginia University, 01 October, https://wvutoday.wvu.edu/stories/2019/10/01/wvu-awarded-5-million-to-continue-rare-earth-project-build-acid-mine-drainage-treatment-facility (Accessed 16 July 2020)La Rivierre, J.R. et al. (1963), The Hanford Isotopes Production Plant Engineering Study, Report no. HW-77770, Richland, WA: General Electric Co. Hanford Atomic Products Operation, United States.Lecomte, M. (2008), Treatment and Recycling of Spent Nuclear Fuel: Actinide Partitioning – Application to Waste Management, CEA Saclay, Paris.Lowe, J.T. (1970), Recovery of 147Pm from Savannah River Plant Waste, USAEC Report DP-1236, Savannah River Laboratory: USAEC, United States.Lowe, J.T. (1969), Isolation of 147Pm by Rapid Cation Exchange Chromatography, Report no. DP-1194, Savannah River Laboratory: US Atomic Energy Commission (USAEC), United States.Lowe, J.T., W.H. Hale and D. Hallman (1971), “Development of a pressurized cation exchange chromatographic process for separation of transplutonium actinides”, Industrial and Engineering Chemistry Process Design and Development, Vol. 10, pp. 131-135, https://doi.org/10.1021/i260037a024. Lumetta, G.J. et al. (2015), “An advanced TALSPEAK concept using 2-ethylhexylphosphonic acid mono-2-ethylhexyl ester as the extractant”, Solvent Extraction and Ion Exchange, Vol. 33, https://doi.org/10.1080/07366299.2014.985920.Lyseid Authen, T. et al. (2022), “An overview of solvent extraction processes developed in Europe for advanced nuclear fuel recycling, Part 2 – homogeneous recycling”, Separation Science and Technology, Vol 57, pp. 1724-1744, https://doi.org/10.1080/01496395.2021.2001531.Malmbeck, R. et al. (2019), “Homogenous recycling of transuranium elements from irradiated fast reactor fuel by the EURO-GANEX solvent extraction process”, Radiochimica Acta, Vol 107, pp. 917-929, https://doi.org/10.1515/ract-2018-3089.McKee, R.W. (1966), An Evaluation of the Prospects for Large-Scale Production of Prometheium-147, Report no. BNWL-310, Richland, Washington, United States, www.osti.gov/servlets/purl/4465079.Modolo, G., A. Geist and M. Miguirditchian (2015) “10 – Minor actinide separations in the reprocessing of spent nuclear fuels: recent advances in Europe”, Taylor, R. (Ed.) Reprocessing and Recycling of Spent Nuclear Fuel, pp. 245-287, Woodhead Publishing, Oxford, https://doi.org/10.1016/C2013-0-16483-5Nilsson, M. and K.L. Nash, (2007), “A Review of the development and operational characteristics of the TALSPEAK process”, Solvent Extraction, and Ion Exchange, Vol. 25:6, pp. 665-701, https://doi.org/10.1080/07366290701634636.Natrajan, L.S. and M.H. Langford Paden (2013), “F-block elements recovery”, in RSC Green Chemistry No. 22, Element Recovery and Sustainability, Royal Society of Chemistry, Cambridge, United Kingdom, https://doi.org/10.1039/9781849737340-00140.Opare, E.O., E. Struhs and A. Mirkouei (2021), “A comparative state-of-technology review and future directions for rare earth element separation”, Renew. Sustain. Energy Rev., Vol. 143, 110917, https://doi.org/10.1016/j.rser.2021.110917.Orr, P.B. (1962), Ion Exchange Purification of Promethium-147 and Its Separation from Americium-241 with Dithylene-Triamine-Pentaacetic Acid as the Eluent, Report no. ORNL-3271, Oak Ridge, TN, Oak Ridge Nuclear Laboratory (ORNL), United States, https://doi.org/10.2172/4819080.Rohrmann, C.A. (1965), Values in Spent Fuel from Power Reactors, Report no. BNWL-25, Richland, WA, BNWL, United States, www.osti.gov/servlets/purl/4618921.Pressly, R.S. et al. (1960), Purification of Kilocurie Quantities of Promethium-147 by Ion Exchange, Report no. ORNL-2928, Oak Ridge, Tennessee, Oak Ridge National Laboratory (ORNL), United States, https://doi.org/10.1016/0022-1902(66)80405-0.Sun, X. et al. (2014), “The optimization of an ionic liquid-based TALSPEAK-like process for rare earth ions separation”, Chemical Engineering Journal, Vol. 239, pp. 392-398, https://doi.org/10.1016/j.cej.2013.11.041.Svantesson, I. et al. (1980), “Distribution ratios and empirical equations for the extraction of elements in Purex high level waste solution—II: HDEHP”, J. Inorg. Nucl. Chem., Vol. 42, 1037, https://doi.org/10.1016/0022-1902(80)80397-6.SMM (2023), Rare Earth Oxides Price, www.metal.com/Rare-Earth-Oxides (accessed on 13 March 2023).Tunsu, C. et al. (2015), “Reclaiming rare earth elements from end-of-life products: A review of the perspectives for urban mining using hydrometallurgical unit operation”, Hydrometallurgy, Vol. 156 (2015), pp. 239-258, http://dx.doi.org/10.1016/j.hydromet.2015.06.007.USAEC (1974), Costs Associated with BNW Promethium Inventories, Letter W.R. Pohlod, Director Finance Division, USAEC, Richland Office to Charles E. Troell, Deputy Assistant Controller for Accounting–Headquarters, USAEC, United States.Weaver, B. and F.A. Kappelmann (1964), TALSPEAK: A New Method of Separating Americium and Curium from the Lanthanides by Extraction from an Aqueous Solution of an Aminopolyacetic Acid Complex with a Monoacidid Organophosphate or Phosphonate, ORNL-3559, Oak Ridge, Tennessee, Oak Ridge National Laboratory (ORNL), United States.Wheelwright, E.J. et al. (1966), Ion Exchange Separation of Kilocurie Quantities of High Purity Promethium, Report no. BNWL-318, Battelle Northwest Laboratory (BNWL), Richland, Washington, United States, https://doi.org/10.2172/4473987.Wheelwright, E.J. and F.P. Roberts (1963), Development and Demonstration of an Ion-Exchange Process for Kilogram-Scale Production of High Purity Promethium, Report no. HW-78651, General Electric Co. Hanford Atomic Products Operation Richland, Washington, United States.Wilden, A. et al. (2017), “An advanced TALSPEAK concept for separating minor actinides. Part 2. Flowsheet test with actinide-spiked simulant”, Solvent Extraction and Ion Exchange, Vol. 35:6, pp. 396-407, https://doi.org/10.1080/07366299.2017.1368945. 8. Zirconium recovery8.1. Zircalloy cladding recovery and reuse The hybrid zirconium extraction (ZIRCEX) process (Gens and Jolley, 1961) utilises hydrochlorination, or chlorination, of the fuel with hydrochloric gas or chlorine gas. This volatilises the zirconium as gaseous zirconium tetrachloride and other constituents of zircaloy from the remainder of the fuel. The zirconium tetrachloride is then oxidised to form zirconium dioxide, which is a more stable form for storage and disposal. Common types of zircaloy cladding, zircaloy-2 and zircaloy-4, contain about 98% Zr, 1.2–1.7% Sn, and fractional percentages of Fe, Cr, and Ni. Trace amounts of other elements including O, N, Hf, Mg, Mn, Mo, W, Ti, and U are also present (Collins and Del Cul, 2009). The advanced alloys like Zirlo and M5 contain about 1% niobium with or without tin; zirconium remains 98–99% (Collins et al., 2013). Zirconium represents about 25% of the mass of spent nuclear fuel as shown in Figure 2.1. Therefore, there is significant interest in reducing the amount of zircaloy requiring expensive geologic disposal.As the zircaloy is nominally hafnium-free, the recovered zirconium is similarly low in hafnium and has a significant value. Nonetheless, 93Zr produced by neutron activation renders the recovered zirconium radioactive. Since 93Zr is long lived (half-life 1.5 × 106 y) and the beta emission is weak, the zirconium may be most suitable for reuse in other nuclear applications, but not as useful to other industries due to long-lived (albeit low) radioactivity. Figure 8.1. Potential insertion of recycled zirconium into the process for zircaloy cladding manufactureSource: NEA EGFRW, 2023.The zircaloy cladding can be separated from the fuel assemblies by different head-end processes. The zirconium can then be separated from alloying components in the zircaloy, and from associated fuel materials, by converting it to volatile zirconium tetrachloride. Figure 8.1 shows how the ZrCl4 can be integrated with a traditional zirconium metal production operation to recycle it into metal. Should recycling be undesirable, the ZrCl4 can be converted to ZrO2 by steam-pyrohydrolysis. The decontaminated ZrO2 is a good form for disposal as low-level waste because of its high stability and resistance to dissolution in groundwater.8.2. Zircaloy recovery from existing hydrometallurgical separationsThe treatment of spent nuclear fuel to recover valuable components requires a head-end process that exposes the component of interest and adjusts the chemical and physical form of those components to be compatible with the processing technology that will be used for the purification and recovery. At present, only zircaloy-clad light water reactor (LWR) fuels are being reprocessed at an industrial scale using hydrometallurgical separations. However, significant research and development efforts, both past and present, are geared to not only the development of hydrometallurgical variants for processing a variety of new fuels that will fuel advanced reactors, but also to the development of “dry” treatments based on pyrochemical, electrochemical and halide volatility processes (Collins et al., 2012). Some of these treatment schemes use a combination of techniques and can be termed as “hybrid” processes.Zircaloy clad fuels are represented primarily by those designed for LWRs, either pressurised water reactors (PWRs) or boiling water reactors (BWRs). In each case, the fuel consists of ceramic-like uranium dioxide (UO2) fuel pellets encased in zirconium-based alloy tubing (e.g. zircaloy), called fuel pins. The PWR and BWR fuel elements differ primarily in the number of fuel pins and in the dimensions of the fuel pins (i.e. diameter and length). The Canada Deuterium Uranium (CANDU) and other pressurised heavy water reactors also use UO2 fuel pellets encased in zircaloy tubes, and although the fuel elements are much smaller in length with fewer fuel pins, they may be processed using similar methods. Hence, it seems reasonable to assume that a future recycling facility, based on a common process chemistry, could be adapted to handle multiple physical forms if desired.The head end of present commercial LWR fuel reprocessing plants include mechanical disassembly and shearing steps, followed by nitric acid dissolution to remove the fuel from the cladding segments (or hulls). Following the dissolution step, the zircaloy cladding hulls are separated and prepared for disposition as a waste requiring geological disposal. Two common methods of preparing the cladding hulls and hardware pieces for disposal are super-compaction and grouting. Alternatively, and as shown in Figure 8.1, cladding hulls can be used as feed material for the recovery of zirconium.The cladding hulls react readily with either anhydrous hydrogen chloride or chlorine at temperatures above 350°C producing volatile zirconium tetrachloride, ZrCl4.Zr + 4HCl = ZrCl4 + 2H2Zr + 2Cl2 = ZrCl4The primary alloying agents such as Sn or Nb and some of the minor components are also volatilised as the chloride. Zirconium dioxide on the inner and/or outer surfaces and other oxide particles embedded in the inner surfaces by fuel cladding interaction or recoil do not react. The volatile zirconium tetrachloride separates from the residual ash, with a high decontamination factor (Collins and Del Cul, 2009), rendering it a low-level radioactive material. ZrCl4 salt is recovered by condensation, and additional sublimation steps may be used to separate it from the SnCl4 or NbCl5 (E. Collins et al., 2013). Volatilisation of the cladding releases the tritium trapped in the cladding. Hydrochlorination with HCl is thought to release the tritium as free hydrogen:ZrTX + 4HCl = ZrCl4 + (2 − x/2)H2 + xTH (x = 1,2)Chlorine releases the tritium as tritium chloride:ZrTX + (2 + x/2)Cl2 = ZrCl4 + xTCl (x = 1,2)An alternative decontamination strategy (Barnes et al., 2019) uses thionyl chloride (SOCl2) as a low temperature chlorination agent (Hecht et al., 1947; North and Hageman, 1912), oxygen sink, and ultimately as a recrystallisation solvent to obtain the tetrachloride product from zircaloy cladding in one step of Figure 8.2. Figure 8.2. Schematic illustration of the process steps in the thionyl chloride zircaloy purification schemeSource: NEA EGFRW, 2023.Chlorination and dissolution of several different zircaloy cladding types is slow (days) in refluxing thionyl chloride but accelerates significantly at temperatures slightly above its boiling temperature, thereby achieving practical rates. Gaseous SOCl2 and sulphur chlorides (SCl2, S2Cl2, Cl2+S) are also effective chlorinating agents. When the final solution is cooled to room temperature the thionyl chloride adduct of zirconium tetrachloride (ZrCl4·SOCl2) is obtained as a crystalline solid (Collins and Drew, 1971). After separating the mother liquor from the solid thionyl chloride adduct, pure ZrCl4 can be obtained by mild heating under vacuum or in a stream of nitrogen (Buscaglione et al., 1987). Thionyl chloride freed by the decomposition can be recycled.Reaction with zirconium metal in zircaloy cladding materials involves oxidation and chlorination, whereas reaction with the metal oxide (ZrO2) only involves exchange of oxygen for chloride. The possible reactions involved are: Zr + 12 SOCl2 → ZrCl4 + 3 S2Cl2 + 6 SO2 + 7Cl2ZrO2 + 2 SOCl2 → ZrCl4 + 2 SO2In both cases formation of sulphur dioxide is one of the main driving forces for these reactions.8.2.1. Zircaloy fuel chemical decladdingOf course, the same chemical dissolution process that is used to treat zircaloy hulls can also be applied to an intact fuel rod, thereby providing an alternative approach to decladding of LWR fuel rods.The volatility of the zirconium and the resistance of the fuel material to common chlorination agents at moderate temperatures (i.e. <400°C) make chemical decladding by chloride volatility an attractive decladding alternative to conventional chopping. Zircaloy cladding is around 98% zirconium metal. Treatment of either segments of fuel pins or entire fuel assemblies with anhydrous HCl, Cl2, converts the zirconium to volatile ZrCl4. The oxide fuel and steel components are not significantly attacked (Del Cul et al., 2012). The gaseous ZrCl4 separates from the fuel and hardware. The remaining fuel pellets are suitable for voloxidation or dissolution processing. Since a fraction of the tritium in spent fuel is bound in the cladding as, presumably, zirconium hydride, vaporisation of the cladding metal matrix releases this tritium.The benefit of using thionyl chloride over other chlorinating agents is that, although thionyl chloride reacts readily with both metals and metal oxides such as UO2, it is at very different rates to that with zirconium. Hence this may allow the selective dissolution of the zircaloy cladding under mild conditions without attacking the fuel (North and Hageman, 1912). The chlorination product from the cladding, ZrCl4, is very soluble in thionyl chloride and may, therefore, be removed from undissolved fuels by filtration. Pure ZrCl4 can then be obtained by mild heating under vacuum or in a stream of nitrogen, and the liquid thionyl chloride can be recycled. A schematic overview of this thionyl chloride decladding procedure is shown in Figure 8.3. Sulphur chloride, S2Cl2 is also very effective and can be used in place of thionyl chloride. Figure 8.3. Schematic of the thionyl chloride chemical decladdingSource: NEA EGFRW, 2023.Oxidation is another chemical decladding method. Oxidation is used in the voloxidation process to separate tritium from the fuel but the accompanying comminution of the fuel releases it from the short cladding segments as a side benefit, enabling mechanical separation (e.g. sieving) of the cladding from the powdered oxide fuel.8.3. ReferencesBarnes, C. et al. (2019), “New reconditioning strategies for spent nuclear fuel rods”, Transactions, Vol. 120/1, pp 136, American Nuclear Society, Westmont, Illinois.Buscaglione, I., C. Stables and H. Sutcliffe (1987), “The reaction of zirconium oxide chloride octahydrate with thionyl chloride”, Inorganica Chimica Acta, Vol. 128, Issue 1, pp. 7-9, https://doi.org/10.1016/S0020-1693(00)84686-1.Collins R.K. and M.G.B. Drew (1971), “Crystal and molecular structure of Di-p-chloro-bis[trichloro(thionyl chloride)zirconium(IV)]”, J. Chem. Soc. A (1971), 3610-3613.Collins, E.D. and G.D. Del Cul (2009), “A practical solution to used nuclear fuel recycling”, in Integrated Radioactive Waste Management in Future Fuel Cycles, Charleston, SC, November 2009.Collins, E.D. et al. (2012), “Process development studies for zirconium recovery/recycle from used nuclear fuel cladding”, Procedia Chemistry, (2012) Vol. 7, pp. 72-76, https://doi.org/10.1016/j.proche.2012.10.013.Collins, E.D. et al. (2013), “Feasibility study to combine chemical decladding and zirconium recovery and recycle”, in: ANS 2013 Winter Meeting, Washington, DC, November 2013.Del Cul, G.D. et al. (2012), “Dry pretreatment of used nuclear fuel to simplify storage or recycle ― shearing or chemical decladding and voloxidation”, Trans. Am. Nucl. Soc., Vol. 107, p. 246, 2012 ANS Winter Meeting, San Diego, CA.Gens, T.A. and R.J. Jolley (1961), New Laboratory Developments in the Zircex Process, ORNL-2992, , Oak Ridge National Laboratory, Oak Ridge, Tennessee, United States, https://doi.org/10.2172/4000618.Hecht, H., G. Jander and H. Schlapmann, (1947), “Über die Einwirkung von Thionylchlorid auf Oxyde (Action of thionyl chloride on oxides)”, Z. Anorg. Chem., Vol. 254, 255264, http://dx.doi.org/10.1002/zaac.19472540501.North, H.B. and A.M. Hageman (1912), “The action of thionyl chloride on metals and metalloids”, J. Am. Chem. Soc., Vol. 34, pp. 890-894, https://doi.org/10.1021/ja02208a007.9. Industrial applications of isotopes9.1. IntroductionThis report has so far focused on describing the potential applications and strategies for recovering isotopes and critical materials from spent fuels, organised by the chemical properties of the elements concerned. This has covered most of the key actinides and fission products that could be recycled for reuse in applications other than as new nuclear fuel materials. The final chapters of this report take a different approach to cover some broader applications of radioisotopes or other components that could be obtained from spent nuclear fuels. Many of these isotopes are also obtainable from other sources and their recovery from spent nuclear fuels for various industrial, research or medical applications is probably of niche value only. Nevertheless, some opportunities exist and, therefore, to ensure these applications and opportunities are not over-looked, the next three chapters will succinctly address relevant aspects of the industrial and medical applications of isotopes and the recycling of other hardware components from spent fuels.9.2. Isotope productionIn practically all sectors of human activity and in most countries of the world there are isotope applications, from 241Am source used in smoke detectors in domestic homes to 60Co in industrial radiography and the wide variety of isotopes used for medical treatments (see Chapter 10). To meet this demand, a complex and worldwide supply industry has grown that continues to evolve, driven by commercial demand but also the availability of research reactors and accelerators where many isotopes are produced. The World Nuclear Association (WNA) identifies the main isotope suppliers as being Mallinckrodt Pharmaceuticals (Ireland), Nordion (Canada), The National Institute for Radioelements (IRE) (Europe), NTP Radioisotopes SOC Ltd (South Africa), Isotope JSC a subsidiary of Rosatom State Atomic Energy Corporation (Russia), and Australian Nuclear Science and Technology Organisation (ANSTO) (Australia) (WNA, 2021).Most medical radioisotopes made in nuclear reactors are sourced from relatively few research reactors, including:High flux Reactor (HFR) at Petten in Netherlands (supplied via IRE and Mallinckrodt);Belgian Reactor 2 (BR-2) at Mol in Belgium (supplied via IRE and Mallinckrodt);Maria in Poland (supplied via Mallinckrodt);Orphée at Saclay in France (supplied via IRE);FRJ-2/FRM-2 at Jülich in Germany (supplied via IRE);LVR-15 at Řež in Czechia;High flux engineering test reactor (HFETR) at Chengdu in China;Safari in South Africa (supplied from NTP);Open Pool Australian Light water (OPAL) reactor in Australia (supplied from ANSTO to domestic market, exports from 2016);Egyptian Second Research Reactor (ETRR-2) in Egypt (forthcoming: supplied to domestic market);Dimitrovgrad in Russia (Isotop-JSC).While information on research reactors and accelerators in operation in the world is available, for example in International Atomic Energy Agency (IAEA) publications (IAEA, 2020), it is difficult to track their real activities in isotope production. In research reactors, isotopes are obtained as or from by-products. The producers of isotopes are often independent of reactor operators and have commercial interests to protect. Moreover, accelerators, particularly of high energy, are devoted to scientific research, and isotope production is only a side activity on which comprehensive information is not readily available.In 2000 the NEA undertook a study to provide member countries with a comprehensive and up-to-date survey of isotope uses and production capabilities in the world (NEA, 2004). That study also analysed trends in demand and supply of isotopes to identify issues of interest to governments. The NEA study highlighted several key issues:Public entities own and operate almost all the research reactors, large-scale accelerators and chemical separation facilities being used for isotope production. Governments fund infrastructures for effective production and beneficial uses of isotopes at those facilities and provide education and training of qualified manpower required in the field. A few private sector enterprises own and operate medium-size cyclotrons producing major medical isotopes for commercial supply.For some isotopes, particularly those of short lives or of special specifications, the supply demand balance is a regional issue. Short-lived isotopes must be produced on the end-user’s site, whereas for other isotopes that may be transported over long distances and require highly specialised facilities for their production, adequate supply may be ensured at world level. In most countries, domestic supply relies at least in part on imports. Some isotopes are supplied by a few producers to users distributed worldwide.Many isotope producers rely on target irradiation services provided by reactors operated in foreign countries.At present, most of the isotope production and use is in OECD countries. Demand is increasing in non-OECD countries and their production capabilities might not increase as fast as their demand. Satisfying isotope demand requires exchanges between OECD and non-OECD countries to ensure adequate supply. Thus, the availability of comprehensive information on existing and projected production worldwide capabilities is important. The need for international transport of irradiated targets and separated isotope products calls for international harmonisation of regulations on licensing and controls related to the production, transport and uses of isotopes.Isotope demand is evolving owing to the development of new applications on one side and to the progressive phase out of some uses on the other. As far as production is concerned, most facilities require several years to be built and commissioned, so it is essential to monitor projected demand and planned production capacities at the global level to alleviate the risk of inadequate supply. The demand for stable isotopes is increasing, as they are essential for some applications. The production of large quantities of economically interesting stable isotopes is likely to be ensured if industrial enrichment plants using gaseous centrifuge technology continue to operate. It is, however, necessary to pursue the development of new technologies or plants to separate stable isotopes that cannot be obtained by the centrifuge technology.Inadequate supply of major isotopes produced with reactors, such as 99Mo and 192Ir, would have detrimental impacts in the medical and industrial sectors. Although these isotopes are usually supplied on a commercial basis, it is important that governments keep interest in monitoring the supply of such important isotopes. It is essential to promote basic research in medical, physical and life sciences that require small quantities of diverse isotopes. Some isotopes useful in medical care are produced with high neutron flux reactors and/or special processing facilities, which are very limited all over the world.Governmental policies are instrumental in maintaining adequate production capabilities for the isotopes used in those fields and they need to implement policy measures to ensure adequate supply of isotopes to meet existing and foreseeable demand. Government policies in the field of isotope production and use are likely to be reassessed in the context of economic deregulation and privatisation of industrial sectors traditionally under state control. Additionally, geopolitical factors may limit or remove access to certain reactors, accelerators, and associated isotope fabrication facilities, which may lead to critical supply issues. Consequently, there have been several reviews undertaken to identify the impact of these challenges, such as the review of supply of medical radioisotopes by the UK Parliament (Parliamentary Office of Science and Technology, 2017), or those by the NEA (NEA, 2018; NEA, 2019). Similar reviews have also been produced in the United States (US DOE, 2015; NSAC Isotopes Subcommittee, 2009; National Academies of Sciences, Engineering, and Medicine, 2021).9.3. Industrial applicationsThe industrial use of isotopes covers a wide variety of applications that use many different radionuclides, usually in the form of sealed radiation sources (NEA, 2000). While many of these applications use small amounts of radioactivity and are “niche” markets, there are some large market segments that consume significant quantities of radioactivity, such as radiation processing and industrial radiography. The uses of isotopes in industry may be classified under four main types of applications: nucleonic instrumentation systems; radiation processing, including sterilisation and food irradiation; technologies using radioactive tracers; and non-destructive testing (see Table 9.1).Table 9.1. Isotopes used for radioactive tracing and non-destructive testingIsotopeHalf-lifeProduction methodUses3H12.3 yReactorRadioactive tracer, luminous paints14C5 730 yReactorNucleonic instrumentation, radioactive tracer55Fe2.7 yReactorNucleonic instrumentation (industrial imagining)57Co271.8 dAcceleratorNucleonic instrumentation (industrial imagining)60Co5.3 yReactorSterilisation, food irradiation, nucleonic instrumentation, non-destructive testing (gamma radiography)63Ni100 yReactorNucleonic instrumentation (e.g. explosive detectors)75Se119.8 dReactorNon-destructive testing (gamma radiography)85Kr14.7 hReactorNucleonic instrumentation90Sr/90Y28.8 y/64 hReactorNucleonic instrumentation109Cd462 dReactorNucleonic instrumentation (industrial imagining)137Cs30 yReactorSterilisation, nucleonic instrumentation147Pm2.6 yReactorNucleonic instrumentation169Yb32 dReactorNon-destructive testing (gamma radiography)192Ir73.8dReactorNon-destructive testing (gamma radiography)204Tl3.78 yReactorNucleonic instrumentation210Po138.4 dReactorStatic electricity elimination238Pu87.7 yReactorSpacecraft power source241Am432.2 yReactorNucleonic instrumentation (e.g. smoke detectors), space batteries252Cf2.65 yReactorNucleonic instrumentation (e.g. explosive detectors), neutron radiographyNucleonic instrumentation includes analysis, measurement and control using sealed radioactive sources (incorporated into instrumentation) and non-destructive testing equipment (gamma radiography apparatus). The sources used may be emitters of alpha or beta particles, neutrons, or X-ray or gamma photons. A relatively large number of isotopes are used for these technologies, which constitute the major worldwide applications of isotopes in terms of the number of industrial sectors concerned, the amount of equipment in operation and the number of industrial companies manufacturing such equipment. Radiation processing uses high-intensity, gamma-emitting sealed sources, e.g. 60Co in industrial irradiators. Typically, the activity of these sources is very large, in the 50 PBq range. This is the largest worldwide application of isotopes, in terms of total radioactivity involved. However, a limited number of users and manufacturers are involved.Radioactive tracers (mainly beta or gamma emitters), as unsealed sources in various chemical and physical forms, are used to study various chemical reactions and industrial processes. This category is widely spread across many sectors, including agronomy, hydrology, water and coastal engineering, and the oil and gas industry. Radioactive tracers are used also in research and development laboratories in the nuclear or non-nuclear fields. However, this type of application has less economic significance than nucleonic instrumentation or radiation processing.9.3.1. Nucleonic instrumentationNucleonic instrumentation systems are integrated as sensors and associated instrumentation in process control systems. The major fields of application are physical measurement gauges, online analytical instrumentation, pollution measuring instruments and security instrumentation. Gauges of density, level and weight by gamma absorptiometry are employed in most industries to perform online non-contact and non-destructive measurements. They incorporate 60Co, 137Cs or 241Am sealed sources. For those applications, isotopes are in competition with non-ionising technologies such as radar, and their market share is tending to decrease. However, emerging applications include multi-flow metering in oil exploration. Gauges of thickness and mass per unit area, by beta particle or gamma photons absorptiometry, are used mainly in the industries for steel and other metal sheet, paper, plastics, and rubber using isotopes such as 85Kr, 90Sr/90Y, 137Cs, 147Pm, and 241Am. The use of those isotopes faces competition from technologies based on the use of X-ray generators.Gauges for measuring the thickness of thin coatings, by beta particles back-scattering, incorporating 14C, 90Sr/90Y, 147Pm or 204Tl sealed sources are used essentially for measurements on electronic printed circuits, precious metal coatings in jewellery or electrical contacts in the electromechanical industry. Different sealed sources are incorporated into various online analytical instruments. Sulphur analysers with 241Am sources are used in oil refineries, power stations and petrochemical plants to determine the concentration of sulphur in petroleum products. Systems with 252Cf sources are used in instrumentation for online analysis of raw mineral materials, mainly based on neutron-gamma reactions. Such systems are used for various ores, coal, raw mineral products and bulk cement. Very few manufacturing firms are involved. Some chemical products, like pollutants, pesticides and polychlorinated biphenols, may be detected by gas phase chromatography, coupled with electron capture sensors incorporating 63Ni beta sources. One of the applications in the field of pollution measuring instruments is the use of beta particles for absorptiometry of dust particles collected on air filters to estimate particulate concentration in air. The isotopes involved are 14C and 147Pm. Security instrumentation systems generally based on neutron-gamma (n,) reactions using 252Cf sources are used to detect explosives and/or drugs mainly in airports, harbours and railway stations.Those systems are very reliable and demand from public security authorities is expanding. Only a few companies are developing those systems. Tritium is used to make luminous paints for emergency exit signs. Laboratory or portable systems, including X-ray fluorescence analysers, sensors, and well-logging tools, constitute a stable demand for various isotopes. X-ray fluorescence analysers are used in mines and industrial plants to analyse ores, to determine the nature of alloys and to inspect or recover metals (for example, they are used to find traces of heavy metals in old paint). The isotopes used are 55Fe, 57Co, 109Cd, and 241Am. Humidity/density meters for on-site measurements are used in agronomy and civil engineering. Humidity meters are also used in steel making. These sensors, based on neutron diffusion, sometimes coupled with gamma diffusion, may use 241Am-Be sources (and sometimes 137Cs and 252Cf). Well-logging tools, used by oil and gas prospecting companies for example, are very important in those sectors of activity. Sources of isotopes such as 137Cs, 241Am-Be, and 252Cf are used for measuring parameters like density, porosity, water, or oil saturation of the rocks surrounding the exploration wells. Smoke detectors using 241Am sources in general are installed in many public areas such as hospitals, airports, museums, conference rooms, concert halls, cinemas and aircraft as well as in private houses. They are so widely spread that they represent the largest number of devices based on isotopes in use worldwide.9.3.2. Food irradiationFood irradiation has a very large potential market for a broad variety and large quantities of products. Food irradiation has been endorsed to improve the safety and nutritional quality of food available by reducing bacterial contamination levels and spoilage. Food irradiation has been endorsed by several international governmental organisations such as the World Health Organization (WHO), the Food and Agriculture Organization (FAO) of the United Nations and the International Atomic Energy Agency (IAEA) (WHO, 1999), and by national organisations such as, in the United States, the Food and Drug Administration. Worldwide, an increasing number of food suppliers are seriously considering the use of food irradiation in their processes and the number of countries allowing food irradiation is growing. 9.3.3. Radioactive tracersA tracer is a detectable substance, for instance labelled with a beta or gamma emitter, which has the same behaviour in a process (e.g. chemical reactor, ore grinder, water treatment plant) as the substance of interest.The main areas of use are to study:the mode and efficiency of chemical reactions (in chemical synthesis research laboratories);mass transfers in industrial plants (e.g. in the chemical, oil and gas, mineral products transformation, metallurgy, pulp and paper, water treatment or waste treatment sectors); andthe behaviour of pollutants (dissolved or suspended) in rivers, estuaries, coastal shores, aquifers, waste dumping sites, and oil, gas or geothermal reservoirs.Within industry, radioisotopes are often used as tracers and gauges, capitalising on radioactivity to measure changes within a system (WNA, 2022). Modern applications are often specialist and tend to use specific isotopes in minimal quantities. Table 9.2 summarises some of the applications of the commonly used radioisotopes found in spent fuel. Table 9.2 also indicates the quantity of each isotope in UOX spent fuel.Clearly, significant quantities are available of several of the commonly used industrial isotopes, most notably 137Cs, 90Sr and 241Am. Of these, 241Am is probably of most interest due to its use in batteries (World Nuclear News, 2019) (See also Section 3.2.2). The prevalence of 137Cs and 90Sr in SNF means that there are considerable amounts available globally. The ~30-year half-lives means that sources do not have to be changed frequently and material recovered historically will not be diminishing quickly. In the case of 137Cs there have been concerns raised about it being a security concern for use in “dirty bombs”. This is particularly the case for caesium chloride-based sources due to the potential water solubility of released material (Rump et al., 2021). Consequently, alternative more robust, stable sources such 60Co are preferred. The recovery of these isotopes solely for further industrial applications is not likely to be economic although the use of vitrified 137Cs sources as described in Section 4.1 offers a potential alternative. There may be other reasons for separating out these radionuclides (e.g. to reduce dose in bulk waste stream and to produce a concentrated stream for disposal), in which case the waste hierarchy approach (DEFRA, 2011) (see Figure 2.3) would expect further exploration into whether benefits can be derived from the material before it is consigned for disposal, for example using the decay heat from the concentrated waste.Table 9.2. Industrial radioisotope half-lives, quantities and usesRadioisotopeHalf-lifeQuantity in UOX (g/tHM)Application241Am432.0 y8.09E+02Backscatter gauges, smoke detectors, fill height detectors and in measuring ash content of coal. 137Cs30.2 y1.84E+03Radiotracer technique for identification of sources of soil erosion and deposition, as well as in density and fill height level switches, also for low intensity gamma sterilisation. Used for blood irradiation in India.51Cr27.7 y2.14E-43Label sand to study coastal erosion and used as a tracer to study blood.60Co5.27 y1.05E-01Gamma sterilisation, industrial radiography, density, and fill height switches. 198Au2.7 dNoneLabel sand to study coastal erosion. 3H12.3 y5.07E-02Tracer to study sewage and liquid waste.192Ir73.8 dNoneGamma radiography to locate flaws in metal components. 85Kr10.8 y2.33E+01Industrial gauging. 54Mn312.5 d2.18E-06Predict the behaviour of heavy metal components in effluents from mining waste waters. 63Ni100 y2.32E-02Light sensors in cameras and plasma displays, also electronic discharge prevention and in electron capture detectors for thickness gauges. Component for beta voltaic batteries. 75Se120 d2.92E-22Gamma radiography and non-destructive testing. 90Sr28.8 y7.80E+02Industrial gauging.204Tl3.78 y9.88E-09Industrial gauging.169Yb32 dNoneUsed in gamma radiography and non-destructive testing. 65Zn244 d1.78E-08Predict the behaviour of heavy metal components in effluents from mining waste waters. Based on 10 years cooled, 65 GWd/tHM burn-up UOX fuel.9.4. ReferencesDEFRA (2011), Guidance on applying the Waste Hierarchy, Department for Environment, Food and Rural Affairs, www.defra.gov.uk.IAEA (2020), Annual Report 2020, IAEA, Vienna, www.iaea.org/opic/annual-report-2020.National Academies of Sciences, Engineering, and Medicine, (2021), Radioactive Sources: Applications and Alternative Technologies. Washington, DC: The National Academies Press, https://doi.org/10.17226/26121.NEA (2004), Beneficial Uses and Production of Isotopes, 2004 Update, OECD Publishing, Paris, www.oecd-nea.org/jcms/pl_13874.NEA (2019), The Supply of Medical Isotopes: An Economic Diagnosis and Possible Solutions, OECD Publishing, Paris, https://doi.org/10.1787/9b326195-en.NEA (2018), The Supply of Medical Radioisotopes. 2018 Medical Isotope Demand and Capacity Projection for the 2018-2023 Period, OECD Publishing, Paris, www.oecd-nea.org/jcms/pl_19862.NSAC Isotopes Subcommittee (2009), Compelling Research Opportunities using Isotopes, NSAC Isotopes Subcommittee, United States, https://doi.org/10.2172/958307.Parliamentary Office of Science and Technology (2017), Houses of Parliament, Parliamentary Office of Science & Technology, POSTnote Number 558 July 2017 Supply of Medical Radioisotopes.Rump, A. et al. (2021), “Estimation of radiation-induced health hazards from a “dirty bomb” attack with radiocesium under different assault and rescue conditions”, Mil Med Res., Vol. 8(1): 65, https://doi.org/10.1186/s40779-021-00349-w. US DOE (2015), Meeting Isotope Needs and Capturing Opportunities for the Future: The 2015 Long Range Plan for the DOE-NP Isotope Program, NSAC Isotopes Subcommittee, United States DOE.WHO (1999), High-Dose Irradiation: Wholesomeness of Food Irradiated with Doses Above 10 kGy, Report of a Joint FAO/IAEA/WHO Study Group, WHO Technical Report Series No. 890, World Health Organization, Geneva.World Nuclear News (2019), “UK generates usable electricity from americium”, https://world-nuclear-news.org/Articles/UK-generates-usable-electricity-from-americium (Accessed 23 July 2020).WNA (2021), “The Many Uses of Nuclear Technology – Supply of radioisotopes”, www.world-nuclear.org/information-library/non-power-nuclear-applications/overview/the-many-uses-of-nuclear-technology.aspx (Accessed 10 September 2023).10. Medical applications of isotopesMedical radioisotopes have been identified as a critical resource in recent years as their production at high purity is difficult and demand is ever increasing. According to an NEA report published in 2018 (NEA, 2018), the market growth rate is estimated to be 0.5% for mature markets and 5% for developing markets. The difficulties of the market for medical isotopes and their production are explored in a 2019 NEA report, which specifically focused on the use and substitutability of technetium-99m (99mTc) in healthcare and the main economic reasons behind its unreliable supply; 99mTc is an essential product for health systems, being used in 85% of all nuclear medicine diagnostic scans performed worldwide (NEA, 2019). However, the generation of 99mTc depends on the production of molybdenum-99. Unfortunately, these radioisotopes have short half-lives, of 66 hours for 99Mo and only 6 hours for 99mTc, and thus must be produced continuously; any disruptions in the supply chain of these medical isotopes lead to cancellations or delays in important medical procedures.In addition, there is the related issue of geographical location – suppliers are located near industrial centres, making it difficult to distribute the isotope to remote locations while it is still effective. The supply of medical isotopes is further complicated by there being a small number of producers across the world. These are frequently government-funded research reactors and cyclotrons rather than fully commercial facilities, and this government-related ownership leads to it being difficult for fully commercial prices for the isotopes to be charged and all costs recovered (NEA, 2019). Most of these facilities are ageing and require more frequent maintenance, resulting in an extended supply shortage. As a result, supplementation of the current supply should be considered.Table 10.1 attempts to summarise some of the most common medical radioisotopes and their uses and the quantities of these targets present in the spent UOX waste stream. Because of the need to obtain the desired isotopes at high purity, it is not surprising, therefore, that medical isotopes are normally produced by irradiation of a target isotope to achieve the necessary product quality. Therefore, rather than just looking for the medical isotopes in SNF it is probably more useful to look for recovery of the target isotopes that can subsequently be used to generate the medical isotope in a dedicated irradiation system.The list in Table 10.1 is not comprehensive in that it is only based on the prevalence of isotopes at a single point in time (i.e. after 10-year cooling) and not on what isotopes will occur through in-growth after irradiation. Similarly, in Table 10.2, which shows the concentration in SNF of target isotopes commonly used to obtain medical grade isotopes, there is no consideration of isotopes arising from decay chains.Of the medical radioisotopes listed in Table 10.1, most are not present in spent fuel in significant quantities, and only 137Cs, 60Co and 90Y exceed 0.1 g/tHM. While 137Cs and 60Co would be easy to recover given their long half-lives (30.2 and 5.3 years, respectively), 90Y with a half-life of 64 hours might appear more difficult but it is milked from the longer lived 90Sr (28.8 years). Similarly, Table 10.2 shows that the prevalence of most of the target isotopes is very low. Only 39 of the 88 isotopes listed are present at the level of 1 g/tHM or above.This is probably not surprising as many of the medical radioisotopes or their precursor isotopes have very short half-lives. Ten-year cooled SNF is likely to have lost most of the species formed during irradiation in the reactor, though, as highlighted above, decay chains will lead to other isotopes arising due to in-growth. Where the isotopes of interest are present in quantities that are sufficient to make recovery viable, the technical issues may be too difficult due to all the other elements present, many of which may have similar chemical behaviour. This issue is complex and much depends on what level of impurity can be tolerated and allows a suitable extraction process to be implemented. Since this depends on very specific issues that differ between the various isotopes, further discussion of these issues or potential extraction processes is beyond the scope of this report.Table 10.1. Medical radioisotope half-lives, quantities and usesRadioisotopeHalf-lifeQuantity in UOX (g/tHM)Application213Bi46 min8.90E-13Used for targeted alpha therapy, due to its high energy emission (8.4 MeV).137Cs30 yr1.84E+03Used for low intensity sterilisation of blood samples.51Cr28 d2.14E-43Used to label red blood cells for monitoring.60Co5.27 yr1.05E-01Used for sterilisation and brain cancer treatment, due to high specific activity. 59Fe46 d1.10E-28Used in studies of iron metabolism in the spleen. 212Pb10.6 h1.77E-07Used in targeted alpha therapy, as the decay chain provides 212Bi and 212Po as alpha emitters. 177Lu6.7 d5.45E-18Used as an imaging and therapeutic radionuclide, as it is a low gamma and beta emitter. 32P14 d3.3317E-12Used in the treatment of a type of blood cancer as a beta emitter. 223Ra11.4 d1.785E-09Used for targeted alpha cancer therapy as a soft x-ray emitter. 75Se120 d2.92E-22Used to study the production of digestive enzymes.89Sr50 d4.41E-21Used for reducing pain of prostate and bone cancer and beta emitters. 227Th18.7 d2.93E-09Used for targeted alpha therapy as it decays to 223Ra. 90Y64 h1.96E-01Used for cancer therapy and as silicate colloid for relieving the pain of arthritis in larger joints due to beta emissions. 225Ac10 d2.97E-10Used for targeted alpha therapy in prostate cancers. 57Co272 d7.33E-10Used as a marker to estimate organ size. Based on 10 years cooled, 65 GWd/tHM burn-up UOX fuel.Table 10.2. Quantity of medical target radioisotopes in spent nuclear fuel (SNF)RadioisotopeQuantity in UOX waste stream in g/tHMRadioisotopeQuantity in UOX waste stream in g/tHM107Ag8.16E-02231Pa6.74E-0327Al2.18E+01102Pd1.07E-0875As2.28E-01141Pr2.16E+03209Bi5.55E-05226Ra4.99E-0743Ca1.31E-0285Rb2.14E+02108Cd4.02E-02103Rh7.40E+02110Cd1.46E+02104Ru1.15E+03111Cd5.02E+0132S1.19E-03112Cd2.46E+0145Sc5.44E-04114Cd2.64E+0176Se1.12E-02116Cd1.00E+0177Se1.47E+0050Cr6.65E-01115Sn4.74E-0152Cr1.42E+01116Sn7.62E+00133Cs2.00E+0386Sr1.22E+0063Cu1.67E+0088Sr6.31E+0265Cu7.79E-0190Sr7.80E+02164Dy7.13E-0199Tc1.42E+0354Fe1.38E+01123Te1.43E-0256Fe2.24E+02124Te1.96E+0069Ga1.23E-03125Te3.52E+0172Ge1.58E-02130Te7.34E+02127I8.44E+01232Th1.71E+01113In1.64E-01169Tm1.50E-0282Kr1.42E+00238U9.06E+0555Mn2.09E+0051V1.66E+01100Mo1.83E+03124Xe5.56E-2092Mo6.61E-01131Xe5.13E+0294Mo4.21E-0189Y8.54E+0293Nb1.73E-03168Yb6.97E-10148Nd7.31E+02176Yb9.36E-0558Ni1.15E+0164Zn5.37E-0160Ni5.06E+0066Zn3.19E-0161Ni2.49E-0167Zn4.43E-0262Ni6.43E-0168Zn2.18E-0164Ni1.96E-0170Zn9.97E-0318O3.02E+0290Zr2.76E+02 Based on 10 years cooled, 65 GWd/tHM burn-up UOX fuel.10.1. ReferencesNEA (2019), The Supply of Medical Isotopes: An Economic Diagnosis and Possible Solutions, OECD Publishing, Paris, www.oecd.org/els/the-supply-of-medical-isotopes-9b326195-en.htm.NEA (2018), The Supply of Medical Radioisotopes: 2018 Medical Isotope Demand and Capacity Projection for the 2018-2023 Period, OECD Publishing, Paris, www.oecd-nea.org/jcms/pl_19862.11. Hardware component recycleIn addition to cladding, spent nuclear fuel contains significant amounts of structural materials such as end fittings, grid spacers and guide tubes that are generically termed hardware. The specific nature of the hardware varies significantly according to the fuel designs in use and includes various alloys such as stainless steel, Inconel and zircaloy.For aged fuel, most of the gamma-emitting activation products embedded in the hardware components will have significantly decayed (notably 60Co, half-life, t½ = 5.27 y; 54Mn, t½ = 312.2 days; and 125Sb, t½ = 2.77 y) after prolonged storage. The remaining long-lived species may include 14C (t½ = 5,730 y), 59Ni (t½ = 7.5 × 104 y), 63Ni (t½ = 100 y), and 94Nb (t½ = 2 × 104 y). Although these species may be considered a long-term concern for the environment, they are a limited exposure concern and may be allowed for surface disposal as low-level waste.The current industrial practice for reprocessing is to remove the heavy end-piece nozzles and chop the remaining bundle of fuel pins into small pieces (2.5-7.6 cm long). The resulting segmented material is then leached with concentrated nitric acid to dissolve the oxide fuel. During this step, the hardware that initially contained a small amount of activation products becomes further contaminated with fission products and actinides, either embedded mechanically or sorbed on the surface metal oxide film. The added alpha and gamma contamination significantly complicates the handling and final disposition of this material. As a result, the current practice at the La Hague reprocessing plant is to compact the hardware and cladding in high integrity waste containers like the ones used for vitrified high-level waste (ANDRA, 2016). The practice at the UK’s Thermal Oxide Reprocessing Plant reprocessing plant was to encase the hardware and cladding pieces in a cement grout (IAEA, 1985).A different approach for future recycling plant design, to avoid contamination of the hardware materials with fission products and actinides from the fuel, is to mechanically remove the fuel rods from the spent fuel assemblies (called “debundling”). Such a process was considered in previous studies and was shown to be cost-effective for consolidation of the fuel rods and minimisation of the storage volume (Del Cul et al., 2012). The mechanically separated hardware would be clean enough to be handled without significant shielding, thus making a melt-recast operation economically feasible. Recasting the hardware components to make other nuclear components, such as containers for other waste or cermet waste forms that replace glass, could be a favourable option for ultimate geological disposal.11.1. ReferencesANDRA (2016), Safety Options Report - Operating Part, CG-TE-D-NTE-AMOA-SR1-0000-15-0060.IAEA (1985), Management of Cladding Hulls and Fuel Hardware, Technical Report Series 258, IAEA, Vienna.Del Cul, G.D. et al. (2012), “Dry pretreatment of used nuclear fuel to simplify storage or recycle – Shearing or chemical decladding and voloxidation”, Trans. Am. Nucl. Soc., Vol. 107, p. 246, 2012 ANS Winter Meeting, San Diego, CA.12. Summary and future perspectives12.1. SummarySpent nuclear fuel contains a wide range of elements and isotopes other than the reusable nuclear materials (uranium and plutonium). The recovery and recycling of uranium and plutonium into new fuel is an industrially proven strategy for spent fuel management. Similarly, the recovery and recycling of the minor actinides for burning in reactors (the partitioning and transmutation [P&T] scenario) has been the subject of intensive international research and development (R&D) and various options exist, although these have only been demonstrated at the R&D scale so far. Looking beyond the actinide elements that are suitable for recycling in reactors, there are many other elements and isotopes that have other applications – for example in space power, non-destructive testing and medical science. Almost since the beginning of the nuclear industry, therefore, people have looked for opportunities to access these materials. Often the simplest or most economic methods are by irradiation of specific targets to obtain radioisotopes. Recovering either radioisotopes or stable elements (critical materials) from spent nuclear fuel (SNF) is complex because they are intimately mixed with a huge range of other elements, undesirable isotopes of the same element or other highly radioactive contaminants. While this has been done quite frequently in the past, previous analyses have often considered it uneconomic or too technically complex for implementation. Furthermore, spent fuel management has come to focus mainly on the open fuel cycle, with disposal of spent fuel, rather than on reprocessing and recycling in a closed fuel cycle, again mainly due to near-term economic factors. This has limited opportunities to co-recover other elements or radioisotopes from SNF during reprocessing or waste management operations.Interest remains in how to access valuable elements and isotopes from SNF and, of course, in the drivers of the economic value of the materials, which is increasingly linked to the global geopolitical situation. The costs of recovering these materials will likely change with the advent of new separation technologies and of advanced fuel cycles, where additional processes could be added to an advanced recycling plant in the design stage rather than expensively backfitted to existing plants. There is also an increasing drive for sustainability and the additional societal benefits generated by recovering specific elements or isotopes is becoming increasingly attractive. The recovery of other useful materials from SNF aligns with the goals of the circular economy and the principles of the waste management hierarchy. Such important drivers, coupled with changing scenarios and societies, mean it is important to keep the recovery and recycling of alternative materials from spent nuclear fuels under periodic review. The NEA Expert Group on Fuel Recycling and Waste Technology (EGFRW) has undertaken a task to provide a state-of-the-art summary of the prospects for recycling and reusing materials from spent nuclear fuels.This report summarised the findings from the EGFRW study. It described the background and opportunities and then, in more depth, the recovery options for different materials. These sections were organised according to the position of the elements in the periodic table (actinides, group 1 and 2 elements, noble gases, rare earth elements, platinum group metals, zirconium). Subsequent chapters looked at other structural materials and applications in industry and medical science and the recovery opportunities. SNF contains a wide range of elements and isotopes from the fission process, neutron activation or subsequent radioactive decay during storage. Criteria have been proposed for deciding which constituents may be economically recoverable although this depends on the fuel cycle scenario and so it is difficult to generalise. Most studies target the platinum group metals and rare earth elements as these are critical materials with obvious economic and strategic value. Many countries now have recognised the importance of these and other critical materials to their economies or national security and are developing strategies to ensure supplies. The recycling of actinides for uses other than as nuclear fuels or transmutation targets is limited. They can be used, for example, in smoke detectors, medical applications and industrial process measurements. Perhaps the main interest lies in their applications as radioisotope power sources for spacecraft. Here both 238Pu (produced by irradiation of 237Np recovered from SNF during reprocessing) and 241Am (separated from aged PuO2 produced by SNF reprocessing) have attractive properties and efforts to obtain them are being pursued internationally.Methods for extracting the high heat-generating isotopes of caesium and strontium from high-level waste have been developed, primarily to reduce the heat load of radioactive waste prior to immobilisation and disposal (caesium and strontium can be decayed stored over periods of 100 to 300 years). However, applications also exist – notably the use of 137Cs in vitrified pencils for blood irradiation in India. 90Sr has applications in nuclear medicine and power sources.SNF contains significant quantities of stable 136Xe, which has significant potential commercial value for various applications, including in the semiconductor industry, lighting, space and medical uses. Separation from 85Kr in off-gas streams from reprocessing plants would be needed and new technologies are being developed for this purpose.Unsurprisingly, given the high commercial value of the materials, the presence of platinum group metals, notably palladium, ruthenium and rhodium, within SNF in significant concentrations (i.e. kilogram quantities per tonne heavy metal) has attracted a lot of interest for recovery. However, the strategy for recovery of these materials needs to include periods of decay storage to allow them to meet the free release threshold, which is about 35 years for ruthenium and 50 years for rhodium. Although Pd is still above the threshold at that time, the main source of activity is 107Pd, which is a soft beta emitter, so the recovered Pd could still be used in certain applications. With respect to separation and extraction, a variety of hydrometallurgical methods are highlighted along with an interesting approach based on photo-reduction.SNF is also a rich source of rare earth elements, many of which are deemed critical materials due to their importance in modern technologies and the technical and political challenges affecting their supply. Many minor actinide separation and recovery processes, such as the grouped actinide extraction (GANEX) process and innovative-selective actinide extraction (i-SANEX), partition and separately strip the chemically similar rare earth elements (REEs) into a separate waste stream, providing a viable route to recover these elements. Particular attention has been drawn to the trivalent actinide lanthanide separation by phosphorus reagent extraction from aqueous complexation (TALSPEAK) process, which was originally developed for the separation of Am3+ and Cm3+ from Ln3+ and Y3+ to allow the americium and curium to be further reprocessed. Evolution of the TALSPEAK process, with different combinations of extractants, aqueous complexing agents, buffer solutions, pH values, and temperatures, offers opportunities for better separation effects for REEs from high-level waste arising from plutonium uranium reduction extraction (PUREX). The recovery of promethium-147 (147Pm) in the United States provides a useful case study of how separation techniques for a specific isotope evolve. In 1959 large amounts of 147Pm were separated from the other rare earth fission products by means of cation exchange chromatography using ammonium citrate at pH 3.0 as the complexing eluent. Over the next 20 to 30 years the process was modified as improved extractant chemistry was discovered or different processes were deployed at different sites. The case study also highlights how production was influenced by the demand for 147Pm.Zirconium represents about 25% of the mass of spent nuclear fuel, so it would be interesting if the amount of zircaloy requiring expensive geologic disposal could be reduced by recycling. Although zircaloy has significant value, 93Zr produced by neutron activation renders the recovered zirconium mildly radioactive. Hence, recovered zirconium may be most suitable for reuse in nuclear rather than non-nuclear applications. Processes for zirconium removal and recovery have been proposed based on conversion to volatile zirconium tetrachloride but the economics are not clear. Options also exist for mechanically separating other hardware components for melt-recasting, enabling materials to be reused in nuclear waste management, for example.Other industrial applications of radioisotopes exist, including in nucleonic instrumentation, food irradiation, radioactive tracers and medical applications. Opportunities for recovering these radioisotopes from SNF are subject to the same limitations outlined above but should not be overlooked.One example of a major international programme investigating the potential for recovering other components of SNF is the Japanese government-funded Impulsing PAradigm Change through disruptive Technologies (ImPACT) programme and the study entitled “Reduce and resource recycling of high-level radioactive waste through nuclear transmutation” (2014-2018). The programme aimed to develop transmutation pathways for long-lived fission products (LLFPs) such as 79Se, 93Zr, 107Pd and 135Cs to reduce the radiotoxicity of high-level waste and to develop opportunities for the reuse of valuable materials from spent fuels. This programme was instructive in demonstrating both the scale and ambition needed to pursue a comprehensive, multi-faceted R&D programme in this field. In this regard, more targeted studies on specific elements/isotopes for specific purposes or applications, for example on the recovery of 241Am for space power or 137Cs for blood irradiation, may yield benefits.12.2. PerspectiveWhile these materials have been recovered from spent nuclear fuel in the past, it has generally been considered either too difficult and/or uneconomic to do so at scale. Questions of technical feasibility and economics, however, change over time. Meanwhile, more attention is being paid to societal value, so that the recovery of materials for non-nuclear (e.g. medical) applications as well as the reduction in the radioactive waste burden could improve public acceptance of nuclear energy. Therefore, it is timely to reassess the potential of recycling and reusing components from spent nuclear fuel for uses other than as new nuclear fuels in reactors or accelerator-driven systems.While the justification for reprocessing and recycling spent fuel is typically based on the economic and environmental advantages of reusing special nuclear materials (uranium, plutonium) and reducing radioactive waste for disposal (by transmutation of minor actinides), the valorisation of materials from residual waste provides additional commercial and environmental benefits, in line with the goals of sustainable development and the circular economy. The view of the experts who took part in the work of the EGFRW is that the analysis of future nuclear fuel cycles should include studies of the valorisation of spent fuel. Such studies should consider all possible applications of the materials contained, not just the recycling of uranium and plutonium for nuclear fuel. In the process, these analyses must also account for changing socio-economic factors and the drive towards a more sustainable future.NEA PUBLICATIONS AND INFORMATIONThe full catalogue of publications is available online at www.oecd-nea.org/pub.In addition to basic information on the Agency and its work programme, the NEA website offers free downloads of hundreds of technical and policy-oriented reports. The professional journal of the Agency, NEA News – featuring articles on the latest nuclear energy issues – is available online at www.oecd-nea.org/nea-news.An NEA monthly electronic bulletin is distributed free of charge to subscribers, providing updates of new results, events and publications. Sign up at www.oecd-nea.org/tools/mailinglist/register.Visit us on LinkedIn at www.linkedin.com/company/oecd-nuclear-energy-agency or follow us on X (formerly known as Twitter) @OECD_NEA.9004301080135006. PLATINUM GROUP METALS9004301080135007. RARE EARTH ELEMENTS9004301080135007. RARE EARTH ELEMENTS9004301080135008. ZIRCONIUM RECOVERY9004301080135008. ZIRCONIUM RECOVERY9004301080135009. INDUSTRIAL APPLICATIONS OF ISOTOPES. Based on 50 GWd burn-up MOX fuel.. 237Np also accumulates during long-term storage of spent fuel as it is a decay product of 241Pu, via 241Am.. This example is illustrative but not typical of separated UK plutonium stocks which were stored for significant periods before reprocessing, thus reducing the initial 241Pu content.. Since the time of the Cs recovery at Hanford (1970s-1980s), significant advancements have been in made in separating Cs from alkaline tank waste. This has been done in the context of treating these wastes for disposal at both the Hanford Site and the Savannah River Site. State-of-the-art technology for Cs removal from alkaline solution includes crystalline silicotitanate, spherical resorcinol formaldehyde resin, and Caustic-Side Solvent Extraction. The latter is deployed industrially at the Salt Waste Processing Facility at Savannah River.9004301080135009. INDUSTRIAL APPLICATIONS OF ISOTOPES900430108013500FOREWORDUNLOCKING THE HIDDEN VALUE OF NUCLEAR FUEL: THE SOCIETAL BENEFITS OF DIVERSE MATERIAL RECYCLING, NEA No. 7674, © OECD 2024 PAGE \* MERGEFORMAT 1900430108013500ACKNOWLEDGEMENTSCONTRIBUTING AUTHORS900430108013500 PAGE \* MERGEFORMAT 42UNLOCKING THE HIDDEN VALUE OF NUCLEAR FUEL: THE SOCIETAL BENEFITS OF DIVERSE MATERIAL RECYCLING, NEA No. 7674, © OECD 2024TABLE OF 900430108013500CONTENTS900430108013500TABLE OF CONTENTS PAGE \* MERGEFORMAT 63UNLOCKING THE HIDDEN VALUE OF NUCLEAR FUEL: THE SOCIETAL BENEFITS OF DIVERSE MATERIAL RECYCLING, NEA No. 7674, © OECD 2024UNLOCKING THE HIDDEN VALUE OF NUCLEAR FUEL: THE SOCIETAL BENEFITS OF DIVERSE MATERIAL RECYCLING, NEA No. 7674, © OECD 2024 PAGE \* MERGEFORMAT 1900430108013500LIST OF ABBREVIATIONS AND ACRONYMS900430108013500LIST OF ABBREVIATIONS AND ACRONYMS900430108013500EXECUTIVE SUMMARY900430108013500EXECUTIVE SUMMARY9004301080135001. INTRODUCTION9004301080135001. INTRODUCTION90043010801350010. MEDICAL APPLICATIONS OF ISOTOPES90043010801350010. MEDICAL APPLICATIONS OF ISOTOPES90043010801350011. HARDWARE COMPONENT RECYCLE90043010801350012. SUMMARY AND FUTURE PERSPECTIVES9004301080135002. BACKGROUND9004301080135002. BACKGROUND90043010801350012. SUMMARY AND FUTURE PERSPECTIVESOECD/NEA PUBLISHING, 2 rue André-Pascal, 75775 PARIS CEDEX 169004301080135003. ACTINIDES9004301080135003. ACTINIDES9004301080135004. GROUP 1 AND 2 ELEMENTS9004301080135004. GROUP 1 AND 2 ELEMENTS9004301080135005. NOBLE GASES9004301080135005. NOBLE GASES9004301080135006. 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