Rapid growth in the market for electric vehicles is imperative, to meet global targets for reducing greenhouse gas emissions, to improve air quality in urban centres and to meet the needs of consumers, with whom electric vehicles are increasingly popular. However, growing numbers of electric vehicles present a serious waste-management challenge for recyclers at end-of-life. Nevertheless, spent batteries may also present an opportunity as manufacturers require access to strategic elements and critical materials for key components in electric-vehicle manufacture: recycled lithium-ion batteries from electric vehicles could provide a valuable secondary source of materials. Here we outline and evaluate the current range of approaches to electric-vehicle lithium-ion battery recycling and re-use, and highlight areas for future progress.
The electric-vehicle revolution, driven by the imperatives to decarbonize personal transportation in order to meet global targets for reductions in greenhouse gas emissions and improve air quality in urban centres, is set to change the automotive industry radically. In 2017, sales of electric vehicles exceeded one million cars per year worldwide for the first time1. Making conservative assumptions of an average battery pack weight of 250 kg and volume of half a cubic metre, the resultant pack wastes would comprise around 250,000 tonnes and half a million cubic metres of unprocessed pack waste, when these vehicles reach the end of their lives. Although re-use and current recycling processes can divert some of these wastes from landfill, the cumulative burden of electric-vehicle waste is substantial given the growth trajectory of the electric-vehicle market. This waste presents a number of serious challenges of scale; in terms of storing batteries before repurposing or final disposal, in the manual testing and dismantling processes required for either, and in the chemical separation processes that recycling entails.
Given that the environmental footprint of manufacturing electric vehicles is heavily affected by the extraction of raw materials and production of lithium ion batteries, the resulting waste streams will inevitably place different demands on end-of-life dismantling and recycling systems. In the waste management hierarchy, re-use is considered preferable to recycling (Fig. 1). Because considerable value is embedded in manufactured lithium-ion batteries (LIBs), it has been suggested that their use should be cascaded through a hierarchy of applications to optimize material use and life-cycle impacts2. Markets for energy storage are under development as energy regulators in various locations transition to cleaner energy sources. Energy storage is particularly sought-after in areas where weak grids require reinforcement, where high penetration of renewables requires supply to be balanced with demand, where there is an opportunity for trading energy with the grid and in off-grid applications. Second-use battery projects have started to develop in locations where there is regulatory and market alignment. However, large concentrations of waste—be it for refurbishment, re-manufacture, dismantling or final disposal—can create substantial challenges. A fire in stockpiled tyres in Powys, Wales, for example, smouldered for fifteen years from 1989 to 2004. Since the electrode materials in LIBs are far more reactive than tyre rubber3, without a proactive and economically sound waste-management strategy for LIBs there are potentially greater dangers associated with stockpiling of end-of-life LIBs. Already the number of fires being reported in metal-recovery facilities is increasing4, owing to the illicit or accidental concealment of (consumer) LIBs in the guise of, for example, lead–acid batteries. Among examples of recent major fires are those that took place in metal-recovery facilities in Shoreway, San Carlos, USA, in September 20165, Guernsey in August 2018 and Tacoma, Washington, USA, in September 2018.
Waste may also represent a valuable resource. Elements and materials contained in electric-vehicle batteries are not available in many nations and access to resources is crucial in ensuring a stable supply chain. In the future, electric vehicles may prove to be a valuable secondary resource for critical materials, and it has been argued that high-cobalt-content batteries should be recycled immediately to bolster cobalt supplies6. If tens of millions of electric vehicles are to be produced annually, careful husbandry of the resources consumed by electric-vehicle battery manufacturing will surely be essential to ensure the sustainability of the automotive industry of the future, as will a material- and energy-efficient 3R system (reduce, re-use, recycle). Here we give an overview of the current state of the art and identify some of the important issues relating to the end-of-life management of electric-vehicle LIBs.
Social and environmental impacts of LIBs
If we consider the two main modes of primary production, it takes 250 tons of the mineral ore spodumene7,8 when mined, or 750 tons of mineral-rich brine7,8 to produce one ton of lithium. The processing of large amounts of raw materials can result in considerable environmental impacts9. Production from brine, for example, entails drilling a hole in the salt flat, and pumping of the mineral-rich solution to the surface. However, this mining activity depletes water tables. In Chile’s Salar de Atacama, a major centre of lithium production, 65% of the region’s water is consumed by mining activities9. This affects farmers in the region who must then import water from other regions. The demands on water from the processing of lithium produced in this way are substantial, with a ton of lithium requiring 1,900 tons of water to extract, which is consumed by evaporation9.
By contrast, secondary production would require only 28 tons of used LIBs7,8,10 (around 256 used electric-vehicle LiBs8). The net impact of LIB production can be greatly reduced if more materials can be recovered from end-of-life LIBs, in as close to usable form as possible11. However, in the rapid-growth phase of the electric-vehicle market, recycling alone cannot come close to replenishing mineral supplies12. LIBs are anticipated to last 15–20 years12 based on calendar aging (the aging due to time since manufacture) predictions—three times longer than lead–acid batteries12. Initial concerns regarding resource constraints for LIB production scale-up focused on lithium13; however, in the near term, reserves of lithium are unlikely to present a constraint14,15.
Of greater immediate concern are cobalt reserves16, which are geographically concentrated (mainly in the politically unstable Democratic Republic of the Congo). These have experienced wild short-term price fluctuations and raise multifarious social, ethical and environmental concerns around their extraction, including artisanal mines employing child labour17. In addition to the environmental imperative for recycling, there are clearly serious ethical concerns with the materials supply chain, and these social burdens are borne by some of the world’s most vulnerable people. Given the global nature of the industry, this will require international coordination to support a concerted push towards recycling LIBs and a circular economy in materials18.
Battery assessment and disassembly
The waste-management hierarchy considers re-use to be preferable to recycling (Fig. 1). As considerable value is embedded in manufactured LIBs, it has been suggested that their use should be cascaded through a hierarchy of applications to optimize material use and life-cycle impacts2. Energy stored over energy invested (ESOI)—the ratio between the energy that must be invested into manufacturing the battery and the electrical energy that it will store over its useful life—is a metric used to compare the efficacy of different energy-storage technologies. Clearly, ESOI figures will improve if end-of-life electric-vehicle batteries can be used in second-use applications for which the battery performance is less critical.
Profitable second-use applications also provide a potential value stream that can offset the eventual cost of recycling, and already a healthy market is developing in used electric-vehicle batteries for energy storage in certain localities, with demand potentially outstripping supply. For the moment the economics of the decision whether to recycle or re-use are set firmly in favour of re-use. The main factors are (1) the refurbishment cost of putting the battery into a second-use application and (2) any credit that would accrue as the result of recycling the battery instead; if the second-use price were to fall below the sum of the refurbishment cost and the recycling credit, then recycling would be the economically favoured option19. In time, it is anticipated19 that the supply of used electric-vehicle batteries will far exceed the quantity that the second-use market can absorb. It must be remembered, therefore, that—if disposal to landfill is to be avoided—recycling must be the ultimate fate of all LIBs, even if they first have a second use.
Given that stockpiling of waste batteries is potentially unsafe and environmentally undesirable, if direct re-use of an LIB module is not possible, it must be repaired or recycled. End-of-life LIB recycling could provide important economic benefits, avoiding the need for new mineral extraction20 and providing resilience against vulnerable links21 and supply risks22 in the LIB supply chain. For most remanufacture and recycling processes, battery packs must be disassembled to module level at least. However, the hazards associated with battery disassembly are also numerous23,24. Disassembly of battery packs from automotive applications requires high-voltage training and insulated tools to prevent electrocution of operators or short-circuiting of the pack. Short-circuiting results in rapid discharge, which may lead to heating and thermal runaway. Thermal runaway may result in the generation of particularly noxious byproducts, including HF gas25, which along with other product gases may become trapped and ultimately result in cells exploding23. The cells also present a chemical hazard owing to the flammable electrolyte, toxic and carcinogenic electrolyte additives, and the potentially toxic or carcinogenic electrode materials.
Diagnostics of battery pack, modules and cells
‘State of health’ is the degree to which a battery meets its initial design specifications. Over time as the battery degrades, its performance varies from its initial condition. The units are percentage points, with 100% indicating a state of health that is identical to that of a new battery meeting its design specification. (Some new batteries may leave the factory deviating from design specifications, and having less than 100% state of health.) The ‘state of charge’ is the degree to which a battery is charged or discharged. Again, the units are percentage points, with 0% indicating empty and 100% indicating full).
Battery repurposing—the re-use of packs, modules and cells in other applications such as charging stations and stationary energy storage—requires accurate assessment of both the state of health, to categorize whether batteries are best suited for re-use (and if so, for which applications), remanufacture or recycling, and the state of charge, for safety reasons in some recycling processes. For high-throughput triage and gateway testing of batteries at scale, the optimal approach involves in situ techniques for monitoring cells in service to enable advance warning of possible cell replacement, and module or pack reconditioning, rather than complete repurposing at a low level of state of health owing to a few failing cells.
Electrochemical impedance spectroscopy can give information on the state of health of cells, modules and, potentially, full packs26, and also an indication of aging mechanisms such as lithium plating. Such measurements have the potential to inform a decision matrix for re-use or disassembly and processing and, importantly, to identify potential hazards that would have further consequences for downstream processing. Electrochemical impedance spectroscopy has been researched for gateway testing in primary production, for example, in a large battery production plant in the UK27,28. A number of electric-vehicle manufacturers plan to use similar technologies to manage and maintain electric-vehicle battery packs through the identification and replacement of failing modules in the field. Substantial advantages in cost, safety and throughput time are anticipated if this process can be mostly or fully automated27,29. In future, more advanced diagnostic functionality will be embedded in battery management systems, providing data that can be interrogated at end-of-life.
Challenges of pack and module disassembly
Different vehicle manufacturers have adopted different approaches for powering their vehicles, and electric vehicles on the market possess a wide variety of different physical configurations, cell types and cell chemistries. This presents a challenge for battery recycling. Figure 2 details three different types of battery cell design, and their respective packs from electric vehicles in the marketplace from model year 2014. It can be seen that the three vehicles possess very different physical configurations, requiring different approaches for disassembly, particularly regarding automation. It can be seen in Fig. 2 that at the different scales of disassembly, the format and relative size of the different components differ, presenting challenges for automation. The differing form factors and capacities may also restrict applications for re-use. And finally, Fig. 2 illustrates that manufacturers employ varying cell chemistries (see Fig. 3), which will necessitate different approaches to materials reclamation and strongly affect the overall economics of recycling. Whereas the prismatic and pouch cells have planar electrodes, the cylindrical cells are tightly coiled, presenting additional challenges to separating the electrodes for direct recycling processes.
For repurposing and second-use applications, automotive battery packs are currently dismantled by hand for either the second use of the modules or for recycling. The weights and high voltages of traction batteries mean that qualified employees and specialized tools are required for such dismantling25. This is a challenge for an industry in transition with a shortage of skills. An Institute of the Motor Industry survey found only 1,000 trained technicians in the UK capable of servicing electric vehicles30, with another 1,000 in training. Given there are 170,000 motor technicians in the UK, this represents less than 2% of the workforce. There is concern that untrained mechanics may risk their lives repairing electric vehicles31, and these concerns logically extend to those handling vehicles at the end-of-life. Additionally, it has been suggested32 that manual dismantling, in countries with high labour costs, is uneconomic with respect to revenues from extracted materials or components. Vehicle design has to strike compromises between crash safety, centre of gravity and space optimization, which must be balanced against serviceability25. These conflicting design objectives often result in designs that are not optimized for recyclability, and that can be time-consuming to disassemble manually25.
Automating battery disassembly
Robotic battery disassembly could eliminate the risk of harm to human workers, and increased automation would reduce cost, potentially making recycling economically viable. This is being piloted in a number of current research projects33,34,35,36. Importantly, automation could also improve the mechanical separation of materials and components, enhancing the purity of segregated materials and making downstream separation and recycling processes more efficient. The automation of the dismantling of automotive batteries, however, presents major challenges. This is because robotics and automation in the manufacturing sector rely on highly structured environments, in which robots make pre-programmed repetitive actions with respect to exactly known objects in fixed positions. In contrast, the development of robotic systems that can generalize to a variety of objects, and handle uncertainty, remains a major challenge at the frontier of artificial intelligence research. It is important to consider the complexity of vehicle battery disassembly from this perspective.
At present there is no standardization37 of design for battery packs, modules or cells within the automotive sector, and it is unlikely that this will happen in the near future. Other battery-reliant products, such as mobile phones, have seen an exponential proliferation of different sizes, shapes and types of battery over the past two decades. At present, much of the factory assembly of these batteries is done by human workers and remains unautomated. Their disassembly and waste-handling typically involve even less structured environments, with much greater uncertainties, than a manufacturing assembly line.
Nevertheless, some progress has been made towards automated sorting of consumer batteries. The Optisort system38,39 uses computer vision algorithms to recognize the labels on batteries, and then pneumatic actuators to segregate batteries into different bins according to their type of chemistry. However, Optisort is currently limited to AA and AAA batteries, and a large amount of pre-sorting by hand is needed to separate these from mixed batches of waste batteries, prior to entering the Optisort machine.
The Society for Automotive Engineers and the Battery Association of Japan have both recommended labelling standards for electric-vehicle batteries. Recent algorithms from computer vision research have some capability to recognize objects and materials on the basis of features such as size, shape, colour and texture. However, it could be advantageous for recycling if manufacturers were to (some manufacturers already do) include labels, QR Codes, RfID tags or other machine-readable features on key battery components and sub-structures. Where these provide a reference to an external data source, its utility in aiding the recycling process will depend on the accessibility and format of that data. If proprietary and private, such data are of limited use, but there may be initiatives to move towards standardization and open data formats. A number of companies are considering blockchain technologies to provide whole-life-cycle tracking of battery materials, including information and transparency on provenance, ethical supply chains, battery health and previous use40. China has signalled its intention to track battery materials.
Automated disassembly of electrical goods has also been implemented to some extent in other sectors. For example, Apple has implemented an automated disassembly line for the iPhone 641 that can handle 1.2 million phones per year. This line has 22 stations linked on a conveyor system and can take the iPhone apart in 11 seconds. However, this system can only deal with an iPhone 6 model. Intact phones, of this exact model, must be positioned at the start of the disassembly line, which then uses pre-programmed motions of 29 robots in 21 different cells to dismantle the phone into 8 discrete parts. The LIB is removed by heating the glue which holds the battery in place. Owing to the potential fire hazard, this must take place inside a thermal event protection system, while monitoring the battery using a thermal imaging system.
Unfortunately, 1.2 million phones per year is a drop in the ocean and the Apple disassembly line has been created using conventional industrial automation methods, making it inflexible and incapable of keeping up adaptively with new models and varieties of phones. But building a flexible and adaptable robot disassembly line need not be prohibitively expensive. The challenge is to create control algorithms and software that can make cheap hardware (robot arms cost only several thousands to several tens of thousands of dollars and costs have been steadily decreasing, can work all the time, and have very long service lifetimes) behave flexibly and intelligently to handle hugely complex disassembly problems. If those artificial intelligence challenges can be solved, then the capital investment required to respond to new and changing models could be kept remarkably low (mainly software updates would be needed). Making robots behave intelligently will rely heavily on sensors to enable advanced robotic perception, especially computer vision using three-dimensional RGB-D imaging devices, combined with bespoke sensors from materials and battery experts. The robots will also require tactile and force-sensing capabilities to handle the complex dynamics problems of forceful interactions between the robots and the materials being disassembled.
Owing to the complexity of automotive battery packs, the possibility of collaborative human–robot co-working using a new generation of force-sensitive ‘co-bot’ robot arms33,42 has been suggested. Unlike conventional industrial robots, these co-bots can safely share a workspace with humans, and Wegener33 suggests that the robot could be taught tasks such as unscrewing bolts, while the human handles cognitively more complex tasks. However, this approach does not protect the human worker from battery hazards and even the task of locating a bolt, moving a tool to engage with it, unscrewing and removing it represents a cutting-edge research challenge in robotics and machine vision. Using current industrial robotics methods, the problem only becomes attemptable (but still difficult) provided that the position of the bolt head is always exactly fixed, in a known pose relative to the robot, with very high precision.
State-of-the-art robotics, computer vision and artificial-intelligence capabilities for handling diverse waste materials do exist, and these systems have demonstrated sufficient robustness and reliability to gain acceptance by the UK nuclear industry, for example, in the deployment of artificial-intelligence-controlled, machine-vision-guided robotic manipulation for cutting of contaminated waste material in radioactive environments43. These technologies are now being adapted to the demanding problem of robotic battery disassembly. At different scales of disassembly—pack removal, pack disassembly, module removal and cell separation—different challenges and barriers to automation exist. Some of these are set out in Fig. 4. Computer-vision algorithms are being developed that can identify diverse waste materials and objects44, reliably track objects in complex, cluttered scenes45, and dynamically guide the actions of robot arms46. Dismantling requires forceful interaction between robots and objects, engendering complex dynamics and control problems, such as simultaneous force and motion control47, which is needed for robotic cutting or unscrewing. Dismantled materials must be grasped and manipulated, including fragmented or deformable materials, which pose challenges both to vision systems and autonomous grasp planners. Adjigble et al.48 have recently demonstrated state-of-the-art performance in autonomous, vision-guided robotic grasping of arbitrary objects from random, cluttered heaps. These advances in computer vision, artificial intelligence and robotics fundamentals offer exceptionally promising tools with which to approach the extremely difficult open research challenge of automated disassembly of electric-vehicle batteries.
Stabilization and passivation of end-of-life batteries
Once LIBs have been designated for recycling, the three main processes involved consist of stabilization, opening and separation, which may be carried out separately or together. Stabilization of the LIB can be achieved through brine or Ohmic discharge. In-process stabilization during opening, however, is the current route preferred in industry, as it minimizes costs. This consists of shredding or crushing the batteries in an inert gas such as nitrogen, carbon dioxide, or a mixture of carbon dioxide and argon. State-of-the art physical processing of LIBs in Europe and North America includes the Recupyl8 (France), Akkuser49 (Finland), Duesenfeld50 (Germany) and Retriev51 (USA/ Canada) processes. Large-scale European processes do not currently use stabilization techniques prior to breaking cells open, instead opting for opening under an inert atmosphere of carbon dioxide or argon (with less than 4% molecular oxygen). Opening under carbon dioxide allows for the formation of a passivating layer of lithium carbonate on any exposed lithium metal. The Retriev process differs from the European processes in that it uses a water spray during the opening step51. The water hydrolyses any exposed lithium and acts as a heatsink, preventing thermal runaway during opening.
Discharging through salt solutions or ‘brine’ (seawater has been used previously52,53) is an alternative method that is supposed to render the cells safe via the corrosion and subsequent water leaching into the cells that passivates the internal cell chemistries. Aqueous solutions of halide salts have been shown to result in substantial corrosion at the battery terminal ends, whereas alkali metal salts, such as sodium phosphate, produce much less corrosion with no water penetration, offering the possibility that cells could be assessed and re-used53. This represents a considerably safer discharging method than using seawater; however, competing electrochemical reactions do occur. Oxygen, hydrogen and other gases, such as chlorine (depending upon the salts in the brine), will form at the anode and cathode terminals, and can potentially be collected, though the dangers and difficulties associated with this should not be underestimated. The time for complete discharge is dependent on the solubility of the salt and hence the conductivity of the solution; increasing the temperature will also shorten the discharge time. Once discharge is complete, the cell components can be separated into different materials streams for further processing: steel can or laminated aluminium, separator, anode (graphite, copper, conductive additive), binder and cathode (active material, aluminium, carbon black, binder).
The brine discharge method is not suitable for high-voltage modules and packs, owing to the high rate of electrolysis and vigorous evolution of gases that would occur. However, for low-voltage modules and cells (or once a high-voltage pack has been dismantled into its constituent components) where the electrolysis can be more carefully controlled, this could, in principle, offer a method of discharge in which the hydrogen and oxygen could be recovered for other applications, adding to the cost-effectiveness of the process54. The downside, however, is that contamination of the cell contents threatens to complicate the downstream chemical processes or compromise the value of processed materials streams.
An alternative to the use of salt solutions is direct Ohmic discharge of the battery through a load-bearing circuit. If the electricity can be reclaimed from the discharge, this could offset some of the cost of further processing. To put it into context, the domestic consumption of a standard UK home is up to 4,600 kWh per year. So a 60-kWh battery pack at a 50% state of charge and a 75% state of health has a potential 22.5 kWh for end-of-life reclamation, which would power a UK home for nearly 2 hours. At 14.3 p per kWh, this equates to UK£3.22 per pack, which may seem a modest gain that does not warrant the cost of investing in equipment. However, if it is unrecovered, the energy from discharge must be dissipated, and this will add to the cooling burden of the facility, creating additional costs. Furthermore, an economy of scale is to be anticipated when recycling electric vehicle batteries in bulk. Similarly, reclaimed energy might make a useful contribution to the profitability of repurposing for second use (see section ‘Battery assessment and disassembly’).
LIB cells can be shredded at various states of charge, and from a commercial point of view, if discharged modules or cells are to be processed in this way, discharge prior to shredding adds cost to the processes. Furthermore, exactly what the optimum level of discharge might be remains unclear. Depending on cell chemistry and depth of discharge, over-discharging of cells can result in copper dissolution into the electrolyte. The presence of this copper is detrimental for materials reclamation as it may then contaminate all the different materials streams, including the cathode and separator. If the voltage is then increased again or ‘normal’ operation resumed55, this can be dangerous because copper can reprecipitate throughout the cell, increasing the risks of short-circuiting and thermal runaway.
Current LIB-processing technologies essentially bypass these concerns by feeding end-of-life batteries directly into a shredder or high-temperature reactor. Industrial comminution technologies can passivate batteries directly but recovered battery materials then require a complex set of physical and chemical processes to produce usable materials streams. Pyrometallurgical recycling processes (see section ‘Stabilization and passivation of end-of-life batteries’) at scale may be able to accept entire electric-vehicle modules without further disassembly. However, this solution fails to capture much of the embodied energy that goes into LIB manufacture, and leaves chemical separation techniques with much to do as the battery materials become ever more intimately mixed.
Pyrometallurgical metals reclamation uses a high-temperature furnace to reduce the component metal oxides to an alloy of Co, Cu, Fe and Ni. The high temperatures involved mean that the batteries are ‘smelted’, and the process, which is a natural progression from those used for other types of batteries, is already established commercially for consumer LIBs. It is particularly advantageous for the recycling of general consumer LIBs, which currently tends to be geared towards an imperfectly sorted feedstock of cells (indeed, the batteries can be processed along with other types of waste to improve the thermodynamics and products obtained), and this versatility is also valuable with respect to electric-vehicle LIBs. As the metal current collectors aid the smelting process56, the technique has the important advantage that it can be used with whole cells or modules, without the need for a prior passivation step.
The products of the pyrometallurgical process are a metallic alloy fraction, slag and gases. The gaseous products produced at lower temperatures (<150 °C) comprise volatile organics from the electrolyte and binder components. At higher temperatures the polymers decompose and burn off. The metal alloy can be separated through hydrometallurgical processes (see section ‘Hydrometallurgical metals reclamation’) into the component metals, and the slag typically contains the metals aluminium, manganese and lithium, which can be reclaimed by further hydrometallurgical processing, but can alternatively be used in other industries such as the cement industry. There is relatively little safety risk in this process, as the cells and modules are all taken to extreme temperatures with a reductant for metal reclamation—aluminium from the electrode foils and packaging is a major contributor here—so the hazards are contained within the processing. In addition, the burning of the electrolytes and plastics is exothermic and reduce the energy consumption required for the process. It follows that in the pyrometallurgical process there is typically no consideration given to the reclamation of the electrolytes and the plastics (approximately 40–50 per cent of the battery weight) or other components such as the lithium salts. Despite environmental drawbacks (such as the production of toxic gases, which must be captured or remediated and the requirement for hydrometallurgical post-processing), high energy costs, and the limited number of materials reclaimed, this remains a frequently used process for the extraction of high-value transition metals such as cobalt and nickel57.
Physical materials separation
For reclamation after comminution, recovered materials can be subjected to a range of physical separation processes that exploit variations in properties such as particle size, density, ferromagnetism and hydrophobicity. These processes include sieves, filters, magnets, shaker tables and heavy media, used to separate a mixture of lithium-rich solution, low-density plastics and papers, magnetic casings, coated electrodes and electrode powders. The result is generally a concentration of electrode coatings in the fine fractions of material, and a concentration of plastics, casing materials, and metal foils in the coarse fractions58. The coarse fractions can be put through magnetic separation processes to remove magnetic material such as steel casings and density separation processes to separate plastics from foils. The fine product is referred to as the ‘black mass’, and comprises the electrode coatings (metal oxides and carbon). The carbon can be separated from metal oxides by froth flotation, which exploits the hydrophobicity of carbon to separate it from the more hydrophilic metal oxides59. An overview of how these processes are used by several companies is shown in Fig. 5, which mentions the Recupyl8 (France), Akkuser49 (Finland), Duesenfeld50 (Germany) and Retriev51 (USA/ Canada) processes.
Often, the polymeric binders from the ‘black mass’ components need to be eliminated to liberate the graphite and metal oxides from the copper and aluminium current collectors. Published routes include the use of sonication in a solvent such as N-methyl-2-pyrrolidone (NMP) or dimethylformamide (DMF) to detach the cathode from the current collector60, thermal heat treatment to decompose the binder61,62, or dissolution of the aluminium current collector63. These processes, however, often require high temperatures (60–100 °C) and are relatively slow (3 h). While ultrasound can induce faster delamination (1.5 h), this is still too slow for a continuous-flow process and the required solvent-to-solid mass ratios of 10:1 will not be viable on a commercial scale with these solvents64.
Recent teardowns of cells indicate that manufacturers are transitioning away from fluorinated binders. Many newer batteries are moving toward alternative binders on the anode, such as carboxymethyl cellulose (CMC), which is water-soluble, and styrene butadiene rubber (SBR), which is not water-soluble but is applied as an emulsion that may be easier to remove at end-of-life. There is also work on water-based binder systems for cathodes, but this is proving to be more challenging. Other studies have used cellulose- and lignin-based binders, although many of these are still in the laboratory testing phase65.
Hydrometallurgical metals reclamation
Hydrometallurgical treatments involve the use of aqueous solutions to leach the desired metals from cathode material. By far the most common combination of reagents reported is H2SO4/H2O2 (ref. 66). A number of studies have been carried out in order to determine the most efficient set of conditions to achieve an optimal leaching rate. These include: concentration of leaching acid, time, temperature of solution, the solid-to-liquid ratio and the addition of a reducing agent67. In most of these studies, it was found that leaching efficiency improved when H2O2 was added. Somewhat counterintuitively, it is understood that H2O2 acts as a reducing agent to convert insoluble Co(III) materials into soluble Co(II) through the reaction7:
A range of other possible leaching acids and reducing agents have been investigated68,69,70,71,72. The leached solution may also subsequently be treated with an organic solvent to perform a solvent extraction73,74,75. Once leached, the metals may be recovered through a number of precipitation reactions controlled by manipulating the pH of the solution. Cobalt is usually extracted either as the sulfate, oxalate, hydroxide or carbonate75,76,77,78,79, and then lithium can be extracted through a precipitation reaction forming Li2CO3 or Li3PO480,81. An alternative recycling method describes mechanochemical treatment of materials, where electrode materials are ground with a chlorine compound or complexing agent to produce water-soluble salts of cobalt, which can be separated from insoluble fractions by washing with water82,83.
Most current recycling processes fall under the umbrella of ‘reagent recovery’ because the materials, with sufficient purity, can be re-used not just for resynthesizing the original cathode materials, but also in a range of other applications, such as the synthesis of CoFe2O4 or MnCo2O4 (refs. 84,85,86). Following initial work focused on the leaching and remanufacture of LiCoO2 (ref. 87), work has since moved on to strategies for new cell chemistries, which typically contain multiple transition metals (for example, LiNi1 − x − yMnxCoyO2; NMC). In such cases, once the metals have been leached from the cathode material, either sequential precipitation is employed to recover the individual metals, or the direct remanufacture of the cathode is targeted, such as work to recover NMC88. In this work, after leaching the metals from the cathode, the concentrations of the various metals in solution were measured and adjusted to match those in the target material (1:1:1 Ni:Mn:Co for NMC-111). The same group has applied the technique to NMC with varying metal contents and successfully resynthesized such NMC materials through the production of a precursor hydroxide, NixMnyCoz(OH)2 with x, y and z varying according to the desired final composition of the cathode89.
Other groups have published similar recovery methods with modifications such as additional solvent extraction steps90, lactic acid or urea as an alternative to sulfuric acid (additionally facilitating resynthesis)91,92 as well as investigating the effect of magnesium in the resynthesized material93. The big issues to be addressed with all solvo-metallurgical processes are the volumes of solvents required, the speed of delamination, the costs of neutralization and the likelihood of cross-contamination of materials. Although shredding is a fast and efficient method of rendering the battery materials safe, mixing the anode and cathode materials at the start of the recycling process complicates downstream processing. A method in which anode and cathode assemblies could be separated prior to mechanical or solvent-based separation would greatly improve material segregation. This is one of several key areas where designing for end-of-life recycling promises to have a real impact, but the historic backlog of batteries containing polyvinylidene fluoride (PVDF) as a binder will still need to be processed. It is clear that the current design of cells makes recycling extremely complex and neither hydro- nor pyrometallurgy currently provides routes that lead to pure streams of material that can easily be fed into a closed-loop system for batteries.
The removal of cathode or anode material from the electrode for reconditioning and re-use in a remanufactured LIB is known as direct recycling. In principle, mixed metal-oxide cathode materials can be reincorporated into a new cathode electrode with minimal changes to the crystal morphology of the active material. In general, this will require the lithium content to be replenished to compensate for losses due to degradation of the material during battery use and because materials may not be recovered from batteries in the fully discharged state with the cathodes fully lithiated. So far, work in this area has focused primarily on laptop and mobile phone batteries, as a result of the larger amounts of these available for recycling38. An example of how this recycling route could work has been outlined recently94. Cathode strips, obtained after dismantling spent batteries, were soaked in NMP before undergoing sonication. Powders were either regenerated through simple solid-state synthesis with the addition of fresh Li2CO3 or treated hydrothermally with a solution containing LiOH/Li2SO4 before annealing.
For high-cobalt cathodes such as lithium cobalt oxide (LCO) conventional pyrometallurgical (see section ‘Pyrometallurgical recovery’) or hydrometallurgical (see section ‘Hydrometallurgical recovery’) recycling processes can recover around 70% of the cathode value11. However, for other cathode chemistries that are not as cobalt-rich, this figure drops notably11. A 2019 648-lb Nissan Leaf battery, for example, costs US$6,500–8,500 new, but the value of the pure metals in the cathode material is less than US$400 and the cost of the equivalent amount of NMC (an alternative cathode material) is in the region of US$4,000. It is important, therefore, to appreciate that cathode material must be directly recycled (or upcycled) to recover sufficient value. As direct recycling avoids lengthy and expensive purification steps, it could be particularly advantageous for lower-value cathodes such as LiMn2O4 and LiFePO4, where manufacturing of the cathode oxides is the major contributor to cathode costs, embedded energy and carbon dioxide footprint95.
Direct recycling also has the advantage that, in principle, all battery components20 can be recovered and re-used after further processing (with the exclusion of separators). Although there is substantial literature regarding the recycling of the cathode component from spent LIBs, research on recycling of the graphitic anode is limited, owing to its lower recovery value. Nevertheless, the successful re-use of mechanically separated graphite anodes from spent batteries has been demonstrated, with similar properties to that of pristine graphite96.
Despite the potential advantages of direct recycling, however, considerable obstacles remain to be overcome before it can become a practical reality. The efficiency of direct recycling processes is correlated with the state of health of the battery and may not be advantageous where the state of charge is low97. There are also potential issues with the flexibility of these routes to handle metal oxides of different compositions. For maximum efficiency, direct recycling processes must be tailored to specific cathode formulations, necessitating different processes for different cathode materials97. The ten or so years spent in a vehicle—followed, perhaps, by a few more in a second-use application—therefore present a challenge in an industry where battery formulations are evolving at a rapid pace. Direct recycling may struggle to accommodate feedstocks of unknown or poorly characterized provenance, and there will be commercial reluctance to re-use material if product quality is affected.
The direct recycling route for cathode coatings is also highly sensitive to contamination by other metals, such as aluminium, which results in poor electrochemical performance60. In particular, methods of recovering materials for further physical or chemical separation that involve a high degree of comminution form fine particles of Al and Cu, which are difficult to separate from the electrode coatings. For this reason, processes that do not mechanically stress the electrode foils are favoured in direct recycling, and separation of the materials streams prior to mechanical sorting is preferable. However, methods of removing the electrode binder—typically pyrolysis or dissolution—present further challenges, such as the production of hazardous byproducts such as HF from pyrolysis of the PVDF binder or the use of the highly toxic NMP as a solvent for dissolution. The potential for the undesirable reaction of the PVDF binder with the electrode material appears to be a notable omission in the recycling literature, despite a growing body of research illustrating that PVDF is an excellent low-temperature fluorinating reagent for metal oxides98. Furthermore, recent research suggests that a certain degree of reaction can occur with the cathode even under conditions of normal cell operation99.
Biological metals reclamation
Bioleaching, in which bacteria are harnessed to recover valuable metals, has been used successfully in the mining industry100,101. This is an emerging technology for LIB recycling and metal reclamation and is potentially complementary to the hydrometallurgical and pyrometallurgical processes currently used for metal extraction102,103; cobalt and nickel, in particular, are difficult to separate and require additional solvent-extraction steps. The process uses microorganisms to digest metal oxides from the cathode selectively104 and to reduce these oxides to produce metal nanoparticles105,106. The number of studies that have been performed thus far, however, is relatively small and there is plenty of opportunity for further investigation in this field. The recycling methods discussed are compared in Fig. 6.
Summary and opportunities
The electric-vehicle revolution is set to change the automotive industry radically, and some of the most profound changes will inevitably relate to the management and decommissioning of vehicles at end-of-life. Of chief concern are the complex, high-tech power trains and, in particular, the LIBs. To put this into perspective, electrification of only 2% of the current global car fleet would represent a line of cars—and in due course, of end-of-life waste—that could stretch around the Earth. There is wide acceptance that, for environmental and safety reasons, stockpiling (or worse, landfill) and wholesale transport of end-of-life electric-vehicle batteries are not attractive options, and that the management of end-of-life electric-vehicle waste will require regional solutions.
In the waste management hierarchy, re-use is considered preferable to recycling, in order to extract maximum economic value and minimize environmental impacts. Many companies in various parts of the world are already piloting the second use of electric-vehicle LIBs for a range of energy storage applications. Advanced sensors and improved methods of monitoring batteries in the field and end-of-life testing would enable the characteristics of individual end-of-life batteries to be better matched to proposed second-use applications, with concomitant advantages in lifetime, safety and market value. Even if all the benefits of second-use are realized, however, it must be remembered that recycling (if not landfill) is the inevitable fate of all batteries.
Some recent life-cycle analyses has indicated that the application of current recycling processes to the present generation of electric-vehicle LIBs may not in all cases result in reductions in greenhouse gas emissions compared to primary production107. More efficient processes are urgently needed to improve both the environmental and economic viability of recycling, which at present is heavily dependent on cobalt content. However, as the amount of cobalt in cathodes is reduced for economic and other reasons, to recycle using current methods will become less advantageous owing to the lower value of the materials recovered.
At present, there are low volumes of electric-vehicle batteries that require recycling. As these volumes increase dramatically, there are questions concerning the economies (and diseconomies) of scale in relation to recycling operations58. Pyrometallurgical routes, in particular, suffer from high capital costs, and if full recyclability of LIBs is to be achieved, alternative methods are urgently required, rather than seeking to recycle only the most economically valuable components.
There are a number of lessons that the future LIB recycling industry could learn from the highly successful lead–acid battery recycling industry. As a technology, lead–acid batteries are relatively standardized and simple to disassemble and recycle, which minimizes costs, allowing the value of lead to drive recycling. Unfortunately, for a rapidly developing technology such as electric-vehicle LIBs, such advantages are not likely to apply any time soon.
A number of improvements could make electric-vehicle LIB recycling processes economically more efficient23, such as better sorting technologies, a method for separating electrode materials, greater process flexibility, design for recycling, and greater manufacturer standardization of batteries. There is a clear opportunity for a more sophisticated approach to battery recovery through automated disassembly, smart segregation of different batteries and the intelligent characterization, evaluation and ‘triage’ of used batteries into streams for remanufacture, re-use and recycling. The potential benefits of this are many and include reduced costs, higher value of recovered material streams, and the near elimination of the risk of harm to human workers.
The design of current battery packs is not optimized for easy disassembly. Use of adhesives, bonding methods and fixtures do not lend themselves to easy deconstruction either by hand or machine. All reported current commercial physical cell-breaking processes employ shredding or milling with subsequent sorting of the component materials. This makes the separation of the components more difficult than if they were presorted and considerably reduces the economic value of waste material streams. Many of the challenges this presents to remanufacture, re-use and recycling could be addressed if considered early in the design process.
For direct recycling where purity of the recovered materials is required, a process which involves less component contamination during the breaking stage is important. This would benefit from an analysis of the cell component chemistries, and the state of charge and state of health of the cells before disassembly into the component parts, rather than the production of a mixture of all components. At present, this separation has only been performed at a laboratory scale and usually employs manual disassembly methods that are difficult to scale up economically. The move to greater automation and robotic disassembly promises to overcome some of these hurdles. Issues regarding the binder still need to be resolved, and acid, alkali, solvent and thermal treatments all have their positives and negatives. A cell design for reclamation of materials is extremely appealing, with low-cost water-soluble binders.
We have focused here on the scientific challenges of recycling LIBs, but we recognize that the ‘system performance’ of the LIB recycling industry will be strongly affected by a range of non-technical factors, such as the nature of the collection, transportation, storage and logistics of LIBs at the end-of-life. As these vary from country to country and region to region, it follows that different jurisdictions may arrive at different answers to the problems posed. Research is under way in the Faraday Institution ReLiB Project, UK; the ReCell Project, US; at CSIRO in Australia and at a number of European Union projects including ReLieVe, Lithorec and AmplifII.
Recycling electric-vehicle batteries at end-of-life is essential for many reasons. At present there is little hope that profitable processes will be found for all types of current and future types of electric-vehicle LIBs without substantial successful research and development, so the imperative to recycle will derive primarily from the desire to avoid landfill and to secure the supply of strategic elements. The environmental and economic advantages of second-use and the low volume of electric-vehicle batteries currently available for recycling could stifle the development of a recycling industry in some places. In many nations, the elements and materials contained in the batteries are not available, and access to resources is crucial in ensuring a stable supply chain. Electric vehicles may prove to be a valuable secondary resource for critical materials. Careful husbandry of the resources consumed by electric-vehicle battery manufacturing—and recycling—surely hold the key to the sustainability of the future automotive industry.
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Many of the ideas suggested for recovery of high-value materials will be trialled by the Faraday Institution’s ReLiB fast-start project funded by the Faraday Institution (grant numbers FIRG005 and FIRG006) and by the ReCell Center, at Argonne National Laboratory, funded by the US Department of Energy. We acknowledge the contribution to the creation of the ReLiB project of N. Rowson (Birmingham Centre for Strategic Elements and Critical Materials). We also thank Q. Dai at Argonne National Laboratories for providing additional data for Fig. 6.
The authors declare no competing interests.
Peer review information Nature thanks Anand Bhatt and Matthew Lacey and the other, anonymous, reviewer(s) for their contribution to the peer review of this work.
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Harper, G., Sommerville, R., Kendrick, E. et al. Recycling lithium-ion batteries from electric vehicles. Nature 575, 75–86 (2019). https://doi.org/10.1038/s41586-019-1682-5
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