Impacts associated with the plastic polymers polycarbonate, polystyrene, polyvinyl chloride, and polybutadiene across their life cycle: A review.

Bhedita J. Seewoo: Writing – review & editing, Writing – original draft, Visualization, Validation, Project administration, Methodology, Investigation, Data curation, Conceptualization. Enoch V.S. Wong: Writing – review & editing, Investigation. Yannick R. Mulders: Writing – review & editing, Investigation. Louise M. Goodes: Writing – review & editing, Investigation. Ela Eroglu: Writing – review & editing, Investigation. Manuel Brunner: Writing – review & editing, Visualization. Aleksandra Gozt: Investigation. Priyanka Toshniwal: Investigation. Christos Symeonides: Writing – review & editing, Supervision, Methodology, Conceptualization. Sarah A. Dunlop: Writing – review & editing, Supervision, Methodology, Conceptualization.

This review was funded by Minderoo Foundation, an independent not-for-profit philanthropic organization. Neither the foundation, nor its benefactors, had any influence on the conduct or the findings of this review.

PVC is a thermoplastic polymer with good durability, flexibility and low cost, making it suitable for various applications such as in the building and construction sector, in food packaging, children's toys, furniture, medical devices, and adhesives [ [178] , [179] , [180] , [181] ]. The annual production volume of PVC was 51 Mt in 2019, accounting for 11 % of all polymers in plastic [ 1 ]. There are two main types of PVC, namely rigid or unplasticised PVC (uPVC) and flexible or plasticised PVC (PPVC) , with the main difference being that in contrast to PPVC, uPVC does not incorporate plasticisers (e.g., phthalates) at the compounding step and therefore, no plasticiser leakage/exposure occurs throughout the production, use, or disposal/recycling stages. Both uPVC and PPVC contain other additives such as stabilisers [ 182 ], which are added to PVC resin powder used to form PVC pellets. These additives may migrate/leak throughout the production, use, and disposal/recycling stages of the life cycle of both PPVC and uPVC. Alternatives for PVC are dependent on short-life vs long-life applications and rigid uPVC vs flexible PPVC. Table 4 outlines the life cycle of PVC, providing insights into the pollutants associated with each stage, along with their environmental leakage and human exposure or health impacts. Table 4 Environmental leakage and human health impact factors of polyvinyl chloride (PVC) throughout its life cycle, distinguishing between unplasticised PVC (uPVC) and plasticised PVC (PPVC) where applicable. Table 4 Life cycle stage Plastic pollutants Environmental leakage and/or human exposure/health impacts Extraction of raw materials Extraction of fossil resources – for fossil carbon Greenhouse gases, particulate matter (PM), metal(loid)s, volatile organic compounds (VOCs) such as benzene, toluene, ethylbenzene, and xylene [ 7 ] Emitted during plastic production, transport and/or end-of-life processes [ 7 ], leading to climate, environmental and health impacts [ 14 , 15 ]. Alternatives: Bio-PVC is derived from ethanol obtained from renewable resources such as starch crops, sugar crops and lignocellulosic biomass [ 118 ]. Bio-PVC otherwise still require similar considerations as fossil carbon-based PVC materials for the rest of their life cycle as detailed below. Production & Manufacturing Monomer production Mercury – About 50 metric tons utilised in 2020 [ 183 ] by older technologies that are still operational for chlorine production [ 184 ]; also used as a catalyst for production of vinyl chloride monomer [ 185 ] Highly hazardous chemical, classified as a reproductive toxicant [ 4 , 186 ] – released into the air, water, and landfills from mercury cell plants [ 187 ], leading to occupational exposures [ 188 ], potential exposures in fenceline communities [ 189 ], and potential health impacts, even at low levels [ 190 ]. Asbestos – About 100–800 metric tons [ 191 ] is used by older technologies for chlorine production [ 184 ] per year A carcinogen [ [192] , [193] , [194] ] – released into the air and landfills from asbestos diaphragm cell plants [ 187 ] and there is potential for occupational exposure [ 191 ]. Per- and polyfluoroalkyl substance (PFAS) – PFAS diaphragms or PFAS-coated membranes such as Nafion used in chlorine production [ 185 ] PFAS are known persistent organic pollutants (POPs) with several human health impacts [ 195 , 196 ], including reduced birth weight [ 197 ], increased allergic outcomes [ 198 ], altered thyroid and immune function [ 199 , 200 ], and impaired neurodevelopment [ 201 ] – unregulated and undocumented releases from PFAS diaphragms or PFAS-coated membranes during chlorine gas production [ 187 ]. Nafion by-products are novel PFAS, with evidence of potential human health impacts [ 202 ] – released into the environment [ 203 ], leading to exposure in fenceline communities [ 204 ]. Chlorine gas – used for production of vinyl chloride monomer Inherently hazardous (aquatic toxicity and specific target organ toxicity upon repeated exposure) [ 4 ] and can contribute to the formation of polychlorinated dibenzodioxins and/or dibenzofurans (PCDD/Fs) – can be released into the air [ 187 ]. See health impacts of PCDD/Fs below. Ethylene dichloride – produced as an intermediate during production of vinyl chloride monomer A possible carcinogen [ 4 , 205 ] on the Substance of Very High Concern (SVHC) list by the Registration, Evaluation, Authorisation and Restriction of Chemicals (REACH) [ 70 ] as well as the ChemSec Substitute it Now (SIN) list [ 71 ] – released into the air [ 185 ], leading to exposure and health impacts in workers [ 206 , 207 ] and fenceline communities [ 208 ]. Other chlorinated compounds, including polychlorinated biphenyls (PCBs), hexachlorobutadiene (HCBD), PCDD/Fs, carbon tetrachloride, and chloroform Released into the environment [ 187 , 209 , 210 ] – potential for occupational exposure [ 185 ]; exposure in fenceline communities reported [ 211 ]. PCBs and HCBD are POPs listed in Annex A of the Stockholm Convention for phasing out and eventual elimination and in Annex C for reducing unintentional releases [ 72 ]. PCBs have several known health impacts, including lower birth weight [ 212 ] and increased risk of endometriosis [ 213 ], type 2 diabetes [ 214 ], and breast cancer [ 215 , 216 ]. HBCD has known human and animal toxicity [ 217 ], and is a possible human carcinogen [ 72 ]. PCDD/Fs are POPs listed in Annex C of the Stockholm Convention for reducing unintentional releases with the goal of eventual elimination [ 72 ]. Have several health impacts, including change in body composition [ 218 ] and increased risk of endometriosis [ 213 ] and incidence of type 2 diabetes [ 219 ]. Carbon tetrachloride is a probable carcinogen [ 205 ] on the SIN list [ 71 ] and is an ozone depleting substance with high global warming potential [ 185 ] and hazardous properties [ 220 ], including liver toxicity and cancer [ 221 ]. Chloroform exhibits specific target organ toxicity upon repeated exposure [ 4 ] and is on the SIN list [ 185 ]. It has known human and animal toxicity, including reproductive and developmental toxicity and carcinogenicity [ 222 ]. Polymerisation Azobisisobutyronitrile (AIBN) [ 223 ] – polymerisation initiator Hazardous chemical on the SIN list [ 71 ] – potential for occupational exposure. Monomer production, Polymerisation & Compounding Vinyl chloride – monomer Primary health concern during PVC production [ 224 ]. Known human carcinogen [ 205 ] on the SVHC list [ 225 ] – released into the environment via waste, in air and in water [ 226 ], leading to potential exposure in workers and fenceline communities [ 208 ]. Occupational exposure via inhalation or skin contact can lead to respiratory problems [ [227] , [228] , [229] ], liver damage [ 207 ], and an increased risk of developing cancer [ 224 ], particularly angiosarcoma of the liver [ 225 , 230 ]. Compounding & Conversion of PPVC Phthalates, e.g., diethylhexyl phthalate (DEHP) and di- n -butyl phthalate (DnBP) – plasticisers (PPVC can contain up to 60 % plasticisers [ 226 ]) DEHP and DnBP are a known carcinogenic and reproductive toxicants [ 4 ] on the SIN list [ 71 ]. Released into external environment via air emissions and in water [ 226 ]. Occupational exposures are well documented [ 231 ], as are the health impacts of phthalates, including impaired neurodevelopment [ 232 ], increased risk of type 2 diabetes and insulin resistance [ 98 , 233 ] and reproductive outcomes [ 234 , 235 ]. Bisphenol A (BPA) – antioxidant Endocrine disruptor [ 4 ] – Potential for environmental release and occupational exposure [ 103 ]. Conversion of PPVC and uPVC Hydrogen chloride Emitted into the workplace air (see table IX [ 141 ]), posing risks to workers. Tetramethylsuccinonitrile (TMSN) Shows specific target organ toxicity upon repeated exposure [ 4 ]. Occupational exposure to this decomposition product of AIBN via inhalation can lead to convulsions and hypoglycemia [ 236 ]. Use (consumption) Use of PPVC products Plasticisers such as phthalates (e.g., DEHP and DnBP) and adipates, e.g., di-2-Ethylhexyl adipate (DEHA) Migrates into patients [ 237 , 238 ], food [ 6 , 239 , 240 ], water [ 226 ], and indoor environments [ 185 ], leading to human exposure [ 238 , 241 ]. See health impacts of phthalates above. DEHA is an aquatic toxicant [ 4 ] and a potential endocrine-disrupting chemical [ 242 , 243 ]. Alternatives: Conventional plastics with less concern for human health than PVC (e.g., low-density polyethylene (LDPE), high-density polyethylene (HDPE), polypropylene (PP), polyethylene terephthalate (PET)) are widely used to replace PVC in a range of applications such as food packaging or medical tubing. This can avoid exposure to hazardous PVC additives such as the widely used phthalates. Use of both PPVC and uPVC Stabilisers, e.g., heavy metal stabilisers including organotins and historical use of lead and cadmium Lead and cadmium are carcinogens [ 4 ] on the SVHC [ 70 ] and SIN lists [ 71 ] – migrate from PVC products (higher migration out of the polymer matrix from PPVC than uPVC although migration occurs from both) [ 244 ], posing potential environmental and health hazards [ 7 , 185 ], including increased risk for cardiovascular and renal disease [ [245] , [246] , [247] ]. Organotin exposure is associated with increased risk of congenital cryptorchidism [ 248 ] and can lead to endocrine and metabolic disturbances [ 7 ] – can migrate from PVC products [ 249 ]. BPA Endocrine disruptor [ 4 ] – migrates into water [ 250 , 251 ] and food, especially when the plastic product is exposed to heat or acidic/alkaline solutions due to polymer degradation during use [ 252 ], which can lead to human exposure and impact health. See health impacts above. TMSN Found in and migrates from the final product [ 9 , 146 ], leading to potential for environmental and human exposure. Non-intentionally added substances (NIAS) [ 147 ] Several NIAS such as vinyl chloride tetramer and antioxidant derivatives migrate from PVC products [ 8 , 9 , 108 ] – potential for human exposure and unknown safety. Nonylphenol, which is formed during the degradation of tris(nonylphenol) phosphite, an antioxidant used in PVC [ 244 ], is a known endocrine disrupting chemical associated with increased risk of ovarian, uterine, pituitary, and testicular cancers [ 253 ] – migrate into food and water [ 250 , 251 , 254 ]. Residual vinyl chloride monomer Can be present in and migrate from PVC products [ [255] , [256] , [257] ], leading to human exposure and potential health impacts. See health impacts above. Secondary micro- and/or nanoplastics (MNPs) Migrates (leaches) from PVC products and PPVC MNPs act as a vector for contaminants such as phthalates [ 258 ] – potential for human exposure and health impacts. Disposal (waste management) Alternatives: Bio-based alternatives such as cellulose acetate bioplastic wood, pulp/cotton fibres and polylactic acid (PLA) [ 259 ] have added end-of-life options such as enhanced biodegradability and compostability [ 260 ]. Landfilling Hazardous chemicals, including hydrochloric acid and above-mentioned additives Known to contaminate the air, soil, and groundwater, even long after the landfills are decommissioned [ 244 ]. Littering and mismanaged waste Secondary MNPs Released into the environment [ 261 ] and can leach hazardous chemicals including phthalates from PPVC MNPs [ 262 , 263 ] and heavy metals from both PPVC and uPVC MNPs [ 264 ]. Accidental or uncontrolled fires (e.g., landfill fires, house fires) and burning PVC-insulated cables for copper retrieval Hazardous pollutants such as PM, polycyclic aromatic hydrocarbons (PAHs), heavy metal stabilisers such as lead and cadmium, benzene, chlorine gas, carbon monoxide, hydrogen chloride, SO x , PCBs, and PCDD/Fs. Released into the environment, posing risks to environmental (e.g., acid rain) and human health [ 7 , 244 , [265] , [266] , [267] ]. See health impacts above. Incineration Hazardous pollutants such as PM, PAHs, heavy metal stabilisers such as lead and cadmium, benzene, chlorine gas, carbon monoxide, hydrogen chloride, SO x , PCBs, and PCDD/Fs. Potential for release into the environment depending on the scavenging methods used and whether optimal operation conditions are met [ 244 ]. See health impacts above. Soluble salts, heavy metals, PCBs, and PCDD/Fs. Migrating (leaching) from incineration residues which are landfilled or processed, resulting in both air and soil contamination [ 244 ]. See health impacts above. Alternatives: Conventional plastics (e.g., LDPE, HDPE, PP, PET) do not include chloride ions and do not produce PCBs and PCDD/Fs when incinerated, although other pollutants may be released similar to the above. Mechanical/chemical recycling Monoaromatics, oxygenated VOCs, chlorinated VOCs, hydrochloric acid and additives, such as plasticisers and stabilisers Released into indoor environment [ 268 ] – potential exposure for recycling workers and dispersion into the broader environment due to its inherent instability to thermal and photo-induced stress [ 269 ]. Alternatives: Conventional plastics with less concern for human health and better recyclability than PVC (e.g., LDPE, HDPE, PP, PET) are widely used to replace PVC in a range of applications such as food packaging or medical tubing. This can avoid exposure to hazardous PVC additives such as the widely used phthalates and increase material circularity. Recycled products DEHP and legacy substances (e.g., POP flame retardants, lead, and cadmium) Can be re-introduced into recycled PVC products during recycling [ 185 , 226 ] – potential for exposure. See health impacts above. Landfilling or recycling e-waste (PPVC) Flame retardants, plasticisers, metals and MNPs Hazardous chemicals migrate from e-waste [ 7 ], with waste pickers and informal e-waste recycling workers, including women and children, being particularly exposed [ 270 ], leading to health impacts [ 271 , 272 ]. See health impacts of flame retardants, plasticisers, and heavy metals above. MNPs released into the environment during mechanical recycling of e-waste [ 273 ]. MNPs have unknown safety. Alternatives: Greener alternatives (phthalate-free, plasticiser-free, flame retardant-free, and/or halogen/PVC-free) to PVC cables are emerging [ 274 ]. Health and environmental concerns regarding these alternatives will need to be considered throughout their life cycle. Environmental leakage and human health impact factors of polyvinyl chloride (PVC) throughout its life cycle, distinguishing between unplasticised PVC (uPVC) and plasticised PVC (PPVC) where applicable.

In this review, we explore the known impacts and potential risks to the environment and human health posed by plastics across their life cycle, focusing on four key problematic polymers. By analysing their entire life cycle, we examine how the specific impacts and risks depend on chemical, polymer and product/application aspects of plastic materials. Specifically, we synthesized published evidence on environmental and human health impacts of resource extraction, production and manufacturing, use/consumption, and disposal/waste management of PC, PS, PVC, and polybutadiene rubber. We show that for every plastic polymer examined, there is evidence of environmental leakage, human exposure, and human health impacts at every stage of the life cycle, and we demonstrate that each aspect of plastic – the polymer itself, the chemicals therein, and the product/application – is associated with unique impacts. Considering these findings, fulfilling the Global Plastics Treaty objective of ending plastic pollution [ 328 ] cannot be achieved via effective waste management practices or increased circularity alone. Our findings emphasise the urgent need for a more refined and comprehensive approach to assessing and mitigating the risks associated with the plastics economy. While extensive research and policy focus has been dedicated to understanding and mitigating the global environmental and human health impacts of plastics, these efforts have largely been limited to plastic chemicals (e.g., POPs [ 72 ]), problematic plastic products such as single-use plastic [ 42 , 329 , 330 ] and problematic applications such as primary MNPs in personal care products [ 329 , 330 ]. Less attention has been given to environmental toxicity assessments, human health risk assessments and management of polymers [ 3 ]. Applying a polymer lens is important because several environmental and human health harms are polymer-specific. 1. Monomers can be hazardous. a. Polymerisation is never 100 % and some unreacted/residual monomers remain in and leach from the final plastic product. b. Monomers and oligomers can also be produced from degradation of the polymer during product use. c. Monomers and oligomers can also be produced and released into the environment due to degradation of managed and mismanaged waste. 2. Micro and/or nanoplastic toxicity is dependent on polymer type [ 7 , 68 , 331 , 332 ]. For example, polyvinyl chloride MNPs have shown the greatest particle toxicity in primary human monocytes in vitro (greatest increase in pro-inflammatory cytokine release) [ 64 ]. Importantly, this effect of polymer has been found to be independent of leached chemicals and particle size/shape, with an independent effect of leached chemicals and particle size/shape also demonstrated. 3. Polymers can present barriers to circularity [ 333 ]. The choice of recycling methods, recyclability of the plastics, and quality of the recyclate are affected by the identity of polymers and their combinations (co-polymers, multi-layer). For example, halogenated polymers are less recyclable due to their intrinsic susceptibility to heat. They contaminate recycling streams, leading to the release of toxic chemicals (e.g., volatile organic chemicals released as degradation products). Additionally, use of complex polymer mixtures affects recyclability of the product (e.g., cling films). Monomers can be hazardous. a. Polymerisation is never 100 % and some unreacted/residual monomers remain in and leach from the final plastic product. b. Monomers and oligomers can also be produced from degradation of the polymer during product use. c. Monomers and oligomers can also be produced and released into the environment due to degradation of managed and mismanaged waste. Polymerisation is never 100 % and some unreacted/residual monomers remain in and leach from the final plastic product. Monomers and oligomers can also be produced from degradation of the polymer during product use. Monomers and oligomers can also be produced and released into the environment due to degradation of managed and mismanaged waste. Micro and/or nanoplastic toxicity is dependent on polymer type [ 7 , 68 , 331 , 332 ]. For example, polyvinyl chloride MNPs have shown the greatest particle toxicity in primary human monocytes in vitro (greatest increase in pro-inflammatory cytokine release) [ 64 ]. Importantly, this effect of polymer has been found to be independent of leached chemicals and particle size/shape, with an independent effect of leached chemicals and particle size/shape also demonstrated. Polymers can present barriers to circularity [ 333 ]. The choice of recycling methods, recyclability of the plastics, and quality of the recyclate are affected by the identity of polymers and their combinations (co-polymers, multi-layer). For example, halogenated polymers are less recyclable due to their intrinsic susceptibility to heat. They contaminate recycling streams, leading to the release of toxic chemicals (e.g., volatile organic chemicals released as degradation products). Additionally, use of complex polymer mixtures affects recyclability of the product (e.g., cling films). Therefore, a whole system approach is needed whereby plastics are assessed by viewing through all lenses – polymer, chemical, and product/application. One example of such an approach being taken is the recommendation for a complete phase out of PVC in healthcare by academics [ 334 ] and non-governmental organisations such as Health Care Without Harm [ 238 ]. PVC products, including disposable and short-lived medical materials like respiratory tubing, blood/plasma bags, and IV tubing, frequently contain phthalates like DEHP, which can leach into patients, particularly newborns, resulting in direct exposure [ 237 , [334] , [335] , [336] ]. Exposure to phthalates at vulnerable moments of human development is a serious concern as it can alter development and have lifelong consequences [ 336 ]. To ensure patient safety, Health Care Without Harm recommends substitution of hazardous chemicals (chemical lens). Since continued use of PVC produced using safer alternative plasticisers will not address the environmental and human health risks associated with PVC production and disposal, additional recommendations include the use of PVC-free alternatives (polymer lens) [ 334 ], and prioritisation of the phasing out of PVC medical devices that can result in direct patient exposure to migrating hazardous chemicals (product/application lens) [ 238 ]. To date, while a small portion of the many thousands of plastic-associated chemicals have been regulated [ 333 ], polymers remain largely unregulated [ 3 ]. At the third session of the Intergovernmental Negotiating Committee meeting to develop an international legally binding instrument on plastic pollution, several delegations questioned the need for the Treaty to include controls on polymers of concern, in addition to provisions targeting harmful chemicals and/or products [ 337 ]. Ongoing assessments of what constitutes problematic plastics will be improved by viewing plastics through polymer, chemical, and product/application lenses, offering opportunities to minimise unintended impacts on the environmental and human health across the plastic life cycle. Based on our findings, polymers need separate consideration within the Treaty for future proofing the agreement and in order to adequately fulfill its goal of ending plastic pollution by: 1. Introducing globally binding requirements on transparency of plastic composition. Material transparency and traceability measures proposed for chemicals should also apply to polymers [ 3 ] as they are the main constituents of plastic. Currently, there is a shortage of information that directly associates plastic chemicals with specific types of polymers or polymer types [ 333 ]. 2. Establishing of a Comprehensive Global Inventory of polymers, with classification and registration utilising a grouping approach based on structural features. This will facilitate the identification of polymers requiring regulatory oversight. Various criteria (see Table 1 in Groh et al., 2023 [ 3 ]) are used to classify polymers, but these vary between jurisdictions and many are debated. No global framework exists yet for the identification of plastic polymers that are problematic at some point or throughout their lifecycle. The European Commission is currently developing proposals to identify polymers requiring registration based on specific criteria (molecular weight, ionicity criteria, degradation criteria and hazard criteria) [ 3 ]. 3. Establishing a negative list of polymers of concern for which there is a body of evidence on their toxic effects, in order to minimise their use and enable the phase-out of their use in non-essential and problematic applications. Despite their ubiquitous use, high production volumes and associated exposure risks, plastic polymers have historically been overlooked by regulators worldwide. Several jurisdictions have defined “polymers of low concern” based on intrinsic polymer properties such as molecular weight, which exempt from regulatory/registration requirements [ 3 , 338 ]. 4. Integrating an effective science-policy interface which can keep step with emerging knowledge, respond to industry innovation and avoid regrettable substitution. This will help identify priorities for further research with respect to comprehensive life cycle assessment of polymers, including in terms of environmental and human health impacts of their degradation products (monomers, oligomers, and micro- and nanoplastics), in order to fill critical knowledge gaps. This body can also advise on the creating and updating of criteria, standard testing protocols and listing of existing and new polymers for which environmental and human health risks, including those of degradation products, become known over time. Currently, countries that do regulate plastic polymers often rely on assessment schemes that were developed in the early 1990s [ 3 ]. Introducing globally binding requirements on transparency of plastic composition. Material transparency and traceability measures proposed for chemicals should also apply to polymers [ 3 ] as they are the main constituents of plastic. Currently, there is a shortage of information that directly associates plastic chemicals with specific types of polymers or polymer types [ 333 ]. Establishing of a Comprehensive Global Inventory of polymers, with classification and registration utilising a grouping approach based on structural features. This will facilitate the identification of polymers requiring regulatory oversight. Various criteria (see Table 1 in Groh et al., 2023 [ 3 ]) are used to classify polymers, but these vary between jurisdictions and many are debated. No global framework exists yet for the identification of plastic polymers that are problematic at some point or throughout their lifecycle. The European Commission is currently developing proposals to identify polymers requiring registration based on specific criteria (molecular weight, ionicity criteria, degradation criteria and hazard criteria) [ 3 ]. Establishing a negative list of polymers of concern for which there is a body of evidence on their toxic effects, in order to minimise their use and enable the phase-out of their use in non-essential and problematic applications. Despite their ubiquitous use, high production volumes and associated exposure risks, plastic polymers have historically been overlooked by regulators worldwide. Several jurisdictions have defined “polymers of low concern” based on intrinsic polymer properties such as molecular weight, which exempt from regulatory/registration requirements [ 3 , 338 ]. Integrating an effective science-policy interface which can keep step with emerging knowledge, respond to industry innovation and avoid regrettable substitution. This will help identify priorities for further research with respect to comprehensive life cycle assessment of polymers, including in terms of environmental and human health impacts of their degradation products (monomers, oligomers, and micro- and nanoplastics), in order to fill critical knowledge gaps. This body can also advise on the creating and updating of criteria, standard testing protocols and listing of existing and new polymers for which environmental and human health risks, including those of degradation products, become known over time. Currently, countries that do regulate plastic polymers often rely on assessment schemes that were developed in the early 1990s [ 3 ]. We recommend consideration of the following insights into LCA evaluation practices and development of the Global Plastics Treaty criteria for assessing problematic plastics: • Circularity is usually assessed at a product level, rather than at a polymer level [ 333 ]. The size of the problem should be considered, including high volumes of production, limited re-use and ineffective recycling resulting in high waste production. • A recent report identified over 4,200 known hazardous plastic-associated chemicals, of which about 3,600 are not currently regulated globally [ 333 ]. Hazardous properties of the chemicals used in plastics should be considered (only some are listed in this review). • More than 9,000 chemicals found in plastic lack publicly available information regarding their origins or uses in plastics [ 333 ]. Which plastic-associated chemicals remain in, and can migrate from, the final plastic material should be considered as this can expose individuals to several hazardous chemicals (e.g., heavy metals), that they would not otherwise encounter in typical daily activities. • A range of plastic products have been banned or restricted at regional and national levels due to their high environmental contamination potential (e.g., single-use plastic [ 42 , 329 , 330 ] and primary MNPs in personal care products [ 329 , 330 ]). Given that no single nation possesses the capability to tackle the transboundary issue of plastic pollution, a unified global effort is essential. Evidence for environmental contamination via emissions and disposal in wastewater, land, and air throughout the plastic life cycle should be considered for all plastic products/applications, including through a chemical and polymer lens, as should evidence of the effects from leakage on environmental health. • More than 6300 plastic-associated chemicals have been reported to have a high exposure potential [ 333 ]. While we recommend a hazard-based approach over a risk-based approach due to the scarcity of information of exposure, evidence for human exposure in the general population and evidence of exposure in workers in manufacturing plants, fenceline communities, consumers, and those working in formal and informal waste disposal and recycling facilities should also be considered, as should existence of systematic post-market human biomonitoring to detect human exposure and evidence of associated health impacts. • Lastly, it is important to consider mitigation measures that effectively prevent environmental leakage and human exposure to chemicals. Circularity is usually assessed at a product level, rather than at a polymer level [ 333 ]. The size of the problem should be considered, including high volumes of production, limited re-use and ineffective recycling resulting in high waste production. A recent report identified over 4,200 known hazardous plastic-associated chemicals, of which about 3,600 are not currently regulated globally [ 333 ]. Hazardous properties of the chemicals used in plastics should be considered (only some are listed in this review). More than 9,000 chemicals found in plastic lack publicly available information regarding their origins or uses in plastics [ 333 ]. Which plastic-associated chemicals remain in, and can migrate from, the final plastic material should be considered as this can expose individuals to several hazardous chemicals (e.g., heavy metals), that they would not otherwise encounter in typical daily activities. A range of plastic products have been banned or restricted at regional and national levels due to their high environmental contamination potential (e.g., single-use plastic [ 42 , 329 , 330 ] and primary MNPs in personal care products [ 329 , 330 ]). Given that no single nation possesses the capability to tackle the transboundary issue of plastic pollution, a unified global effort is essential. Evidence for environmental contamination via emissions and disposal in wastewater, land, and air throughout the plastic life cycle should be considered for all plastic products/applications, including through a chemical and polymer lens, as should evidence of the effects from leakage on environmental health. More than 6300 plastic-associated chemicals have been reported to have a high exposure potential [ 333 ]. While we recommend a hazard-based approach over a risk-based approach due to the scarcity of information of exposure, evidence for human exposure in the general population and evidence of exposure in workers in manufacturing plants, fenceline communities, consumers, and those working in formal and informal waste disposal and recycling facilities should also be considered, as should existence of systematic post-market human biomonitoring to detect human exposure and evidence of associated health impacts. Lastly, it is important to consider mitigation measures that effectively prevent environmental leakage and human exposure to chemicals. Overall, there is a need for: • Whole system consideration of environmental and human health impacts of plastic polymers, chemicals, and products/applications throughout the plastic life cycle in the Global Plastics Treaty. • Implementation of stronger regulatory measures to phase out hazardous polymers and chemicals in plastics and promote safer alternatives. • Integration of cost externalities from human health and environmental damage into fossil carbon-based plastics (e.g., via a global plastic levy). • Increasing funding for research and development of sustainable and less hazardous plastic alternatives, particularly for the replacement of the most problematic plastics, with respect to polymers, chemicals, and products/applications. • Fostering collaborative efforts among industry, government, and academia to innovate in sustainable plastic production, recycling technologies, and waste management. • Enhancing public awareness and education on the impacts of plastics to drive informed consumer choices and support sustainable practices. Whole system consideration of environmental and human health impacts of plastic polymers, chemicals, and products/applications throughout the plastic life cycle in the Global Plastics Treaty. Implementation of stronger regulatory measures to phase out hazardous polymers and chemicals in plastics and promote safer alternatives. Integration of cost externalities from human health and environmental damage into fossil carbon-based plastics (e.g., via a global plastic levy). Increasing funding for research and development of sustainable and less hazardous plastic alternatives, particularly for the replacement of the most problematic plastics, with respect to polymers, chemicals, and products/applications. Fostering collaborative efforts among industry, government, and academia to innovate in sustainable plastic production, recycling technologies, and waste management. Enhancing public awareness and education on the impacts of plastics to drive informed consumer choices and support sustainable practices.

The graphical abstract was designed by BJS and MB with the assistance of the Text to Vector Graphic tool in Adobe Illustrator and Dall•E 2. After using these tools, the authors reviewed and edited the content as needed and take full responsibility for the content of the publication.

PS is a thermoplastic polymer made from the styrene monomer. It is a lightweight material and can exhibit high thermal insulation and transparency. Different forms of PS are used in both short- and long-lived applications, such as packaging materials, food containers, insulation, and electronics casings. It is one of the most widely used plastics. The annual production volume of PS was 21 Mt in 2019, accounting for 5 % of all polymers in plastic [ 1 ]. PS can be either solid or foamed and there are four common forms. • Rigid PS refers to solid, non-foamed PS, often used in applications where a solid, durable material is required, such as disposable cutlery, food containers, and packaging trays. • EPS is a lightweight, foamed PS material produced by expanding PS beads with steam, then moulding them into shape. EPS is known for its excellent thermal insulation properties, making it ideal for use in construction as insulation boards, packaging materials, and protective packaging for fragile items. It is also rigid and provides cushioning against impact. • Extruded PS (XPS) is another type of foamed PS, but it is produced through an extrusion process rather than bead expansion, providing it with greater strength, moisture resistance, and thermal insulation properties. It is commonly used in applications where high compressive strength and moisture resistance are required, such as insulation for roofs, walls, and floors in construction. • PS microbeads are tiny spherical particles of PS and are classified as primary microplastics. PS microbeads can provide texture, exfoliation, or abrasiveness in cosmetic products like facial scrubs and toothpaste. Rigid PS refers to solid, non-foamed PS, often used in applications where a solid, durable material is required, such as disposable cutlery, food containers, and packaging trays. EPS is a lightweight, foamed PS material produced by expanding PS beads with steam, then moulding them into shape. EPS is known for its excellent thermal insulation properties, making it ideal for use in construction as insulation boards, packaging materials, and protective packaging for fragile items. It is also rigid and provides cushioning against impact. Extruded PS (XPS) is another type of foamed PS, but it is produced through an extrusion process rather than bead expansion, providing it with greater strength, moisture resistance, and thermal insulation properties. It is commonly used in applications where high compressive strength and moisture resistance are required, such as insulation for roofs, walls, and floors in construction. PS microbeads are tiny spherical particles of PS and are classified as primary microplastics. PS microbeads can provide texture, exfoliation, or abrasiveness in cosmetic products like facial scrubs and toothpaste. There are minimal opportunities to substitute or vary the materials used in PS production [ 117 ]. Table 3 outlines the life cycle of PS, providing insights into the pollutants associated with each stage, along with their environmental leakage and human exposure or health impacts, distinguishing between the different forms of PS where applicable. Table 3 Environmental leakage and human health impact factors of polystyrene (PS) throughout its life cycle, distinguishing between rigid PS, expanded PS (EPS), extruded PS (XPS), and PS microbeads where applicable. Table 3 Life cycle stage Plastic pollutants Environmental leakage and/or human exposure/health impacts Extraction of raw materials Extraction of fossil resources – for fossil carbon Greenhouse gases, particulate matter (PM), metal(loid)s, volatile organic compounds (VOCs) such as benzene, toluene, ethylbenzene, and xylene [ 7 ] Emitted during plastic production, transport and/or end-of-life processes [ 7 ], leading to climate, environmental and health impacts [ 14 , 15 ]. Alternatives: Bio-based PS are made from renewable resources [ 118 ]. However, they have the same issues for consideration for the rest of their life cycle as the fossil carbon-based PS as detailed below. Bio-sourced alternatives like polyhydroxyalkanoates (PHAs) have added end-of-life benefit of being biodegradable/compostable and have the potential to replace PS in certain applications, without the production, use and end-of-life issues related to styrene and PS. Production & Manufacturing Monomer production Benzene - primary chemical needed for production of styrene monomer A carcinogen [ 69 , 119 ] on the ChemSec Substitute it Now (SIN) list [ 71 ] – potential for occupational exposure [ 120 , 121 ]. Monomer production & Polymerisation Styrene - monomer A probable carcinogen [ 122 ] on the SIN list [ 71 ] with known toxicity to animals and possibly hazardous to humans [ [122] , [123] , [124] ] – potential emissions at styrene and PS manufacturing facilities [ 117 ]. Risk of runaway reactions [ 125 ], which have caused numerous injuries and fatalities in multiple events (see Table 1 [ 126 ]). Polymerisation Azobisisobutyronitrile (AIBN) – polymerisation initiator Hazardous chemical on the SIN list [ 71 ] – potential for occupational exposure [ 117 ]. Compounding & Conversion Flame retardants including historical use of brominated flame retardants such as hexabromocyclododecane (HBCD) and polybrominated diphenyl ethers (PBDEs) Flame retardants can be hazardous by nature [ 67 ] – potential for environmental release and occupational exposure. HBCD is bio-accumulative [ 4 ], carcinogenic [ 4 ], and a persistent organic pollutant (POP) [ 117 ] listed in Annex A of the Stockholm Convention for phasing out and eventual elimination [ 72 ]. Environmental emissions [ 127 , 128 ] and occupational exposure (HBCD production and processing plants [ 127 ], PS manufacturing plants [ 129 ] and from thermal cutting of PS [ 130 ]) can lead to environmental and human health risks [ 127 , 131 ], including type 2 diabetes [ 132 ]. PBDEs are POPs with known health impacts [ 7 ], including impaired neurodevelopment [ 133 , 134 ], reduced birth weight [ 135 ] and increased risk of gestational diabetes [ 136 ]. Several PBDEs are on Annex A of the Stockholm Convention for phasing out and eventual elimination [ 72 ]. There is potential for occupational exposure during extrusion and moulding due to high thermal stress [ 137 ]. Alternatives: Substitute flame retardants such as organophosphate esters (OPEs) also have known health impacts [ 7 , 138 ], including neurotoxicity [ 139 ] and altered pregnancy and birth outcomes [ 140 ]. Blowing agents for EPS including historical use of different types of chlorofluorocarbons (CFCs) and hydrochlorofluorocarbons (HCFCs) CFCs and HCFCs are ozone depleting substances with high global warming potential [ 117 ]. May be retained in the final EPS product – potential for environmental release during use and disposal [ 117 ]. Conversion Styrene and other VOCs Emitted into the workplace air (see Tables X and XI [ 141 ]), posing risks to workers. See health impacts above. Use (consumption) Alternatives: Conventional plastics with less concern for human health than PS such as high-density polyethylene (HDPE), polypropylene (PP), and polyethylene terephthalate (PET) are widely used to replace PS in a range of applications. Bioplastics, including bio-derived and biodegradable/compostable bioplastics, are being used as alternatives in some applications such as coffee lids. Styrene Migrates into food [ 142 ] and hot liquids [ 143 ] and is released into air (e.g., when cutting of insulation foam boards) [ 117 ], leading to human exposure and potential health risks. See health impacts above. AIBN Hazardous chemical on the SIN list [ 71 ] – can still be found in the final product [ 144 ], and therefore there is potential for impacts on environmental and human health [ 145 ]. Tetramethylsuccinonitrile (TMSN) Release/migration of this decomposition product of AIBN during use [ 9 , 146 ] – potential for human exposure and health impacts. Styrene dimers/oligomers & other non-intentionally added substances (NIAS) [ 147 ] Release/migration during use [ 108 ] – potential for human exposure and health impacts. Flame retardants including historical use of HBCD Present in indoor environments [ 148 ], leading to inhalation and ingestion exposure [ 117 , 149 ]. See health impacts above. PS microbeads - Primary micro- and/or nanoplastics (MNPs) Leakage and direct human exposure via ingestion, inhalation or potentially absorption via the skin due to use as exfoliants in personal care products [ 150 , 151 ] – potential impacts on the environment [ 152 ] and human health [ 153 ]. Secondary MNPs Migrates (leaches) into food from food contact materials such as plastic food containers [ 154 , 155 ] and food trays [ 156 ], which can lead to human exposure and potential health impacts [ 7 ]. Disposal (waste management) Alternatives: Substitute biodegradable materials for common PS applications are currently emerging since the high volume-to-weight ratio of foamed PS makes it impractical to transport or landfill. These can range from packaging solutions with traditional insulating materials (such as wool [ 157 ]) or new technologies like chitin-based [ 158 ] or starch-based [ 159 , 160 ] (biodegradable) foams. Landfilling PBDE, HBCD, CFC and HCFC Potential for legacy chemicals to migrate from PS in landfills [ 117 , 161 ]. See impacts above. Secondary MNPs Found in landfill leachates [ 162 ] and act as a reservoir of antibiotic resistance genes [ 163 ] – potential for environmental and human health impacts. Littering and mismanaged waste Secondary MNPs Released into the environment (one of the most common MNPs in the marine environment [ 164 ]) – potential impacts on human health [ 153 ] and the environment [ 152 , 165 ]. Flame retardants and other additives Migrating from PS into the environment [ 166 , 167 ] – potential impacts on the environment [ 168 ] and on human health due to indirect exposure from contaminated food products [ 169 , 170 ]. Styrene oligomers & other NIAS NIAS produced from PS degradation and migrate into the environment [ 171 ]. Accidental or uncontrolled fires Styrene monomers, halogenated flame retardants (including HBCD and PBDE), polybrominated dibenzo- p -dioxins and dibenzofurans (PBDD/Fs), sulphur dioxide, nitrogen dioxide, PM, carbon monoxide Released into the environment [ 117 , 137 , 172 ] – potential environmental impacts and exposure can lead to several health impacts [ 7 , 173 ]. See specific health impacts above. PBDD/Fs show reproductive effects and immunotoxicity in animal studies [ 174 , 175 ]. Incineration PBDD/Fs Produced as by-products of brominated flame retardants and released into the environment from malfunctioning incinerators [ 117 ], leading to potential exposure and health impacts in workers and fenceline communities. Recycling Alternatives: Low recycling rate relative to other plastic types [ 176 ], for example, due to the high volume-to-weight ratio of EPS. PS requires a modified process for mechanical recycling compared to other plastics. Consequently, most recycling facilities do not offer PS recycling. Conventional plastics with less concern for human health and better recyclability than PS (e.g., HDPE, PP, PET) can be used to replace rigid PS in a range of applications. Processing Flame retardants including historical use of HBCD and PBDEs and their transformation products under thermal stress (e.g., PBDD/Fs) Potential exposure for recycling workers and dispersion into the broader environment when the material is processed [ 117 , 137 ]. See health impacts above. Recycled products Legacy POPs (e.g., HBCD) Risk of re-introduction into recycled PS product [ 177 ]. See health impacts above. Environmental leakage and human health impact factors of polystyrene (PS) throughout its life cycle, distinguishing between rigid PS, expanded PS (EPS), extruded PS (XPS), and PS microbeads where applicable.

Plastic is ubiquitous in everyday life and in the environment. The annual global production volume of fossil carbon-based plastic reached over 457 million metric tons (Mt) in 2019 and this figure is anticipated to triple by 2060 [ 1 ]. In 2022, the United Nation Environment Assembly endorsed a resolution to end plastic pollution to safeguard the well-being of current and future generations. The resolution incorporates a holistic approach, considering the complete life cycle of plastic, from the extraction of raw materials to production and manufacturing, use and disposal, with the goal of either restricting or improving the systems as necessary within the plastic supply chain. This will be achieved through establishing an international legally binding agreement known as the ‘Global Plastics Treaty’ [ 2 ]. However, comprehensive life cycle assessment (LCA) of plastic, particularly its impact on the environment as well as human health, is complicated by the complex composition of plastics and the diverse array of chemicals involved from cradle to grave. Importantly, despite being the main constituent of plastic, polymers are often overlooked in regulations [ 3 ]. Plastics are complex chemical mixtures which demand a nuanced understanding to highlight their environmental and health impacts. They are a group of predominantly fossil carbon-based, complex, highly heterogeneous, synthetic chemical materials. Plastics are characterised by their ability to be formed into various shapes, typically during manufacturing processes, and can function as a structural component of a final product. They are comprised of at least one type of synthetic or chemically modified natural polymer – made from individual functional chemical units called monomers – and a range of chemicals [ 4 ]. Depending on the polymer matrix, plastics can be grouped into thermoplastics (e.g., polycarbonate, polystyrene) or thermosets (e.g., synthetic rubber, epoxy resins). More than 10,000 different chemicals are used in plastic production, majority of which are known to be hazardous to the environmental and human health or are lacking hazard data to evaluate safety [ 4 ]. The resulting plastic materials have widely varied chemical compositions, including the intended polymer matrix and additives, as well as unreacted monomers, processing aids (e.g., persisting solvents or catalysts), and non-intentionally added substances (NIAS) such as byproducts (e.g., oligomers), impurities/contaminants, as well as degradation and transformation products [ 5 ]. Importantly, chemicals in plastic materials are usually not covalently bound to the polymer matrix and can migrate out of the plastic material [ 6 ]. Environmental and human health are negatively impacted throughout the plastic life cycle due to industrial emissions, occupational risks and local pollution during extraction of raw materials, production and manufacturing of plastic and disposal/waste management as well as due to migrating chemicals and particulates across the plastic life cycle [ 7 ], including during use by consumers [ 8 , 9 ]. Fig. 1 shows the different stages and sub-stages of the plastic life cycle. Briefly, extraction of raw materials is the first stage of the plastic life cycle. Most (99 %) plastic polymers produced globally are derived from fossil carbon [ 10 ]. Oil and gas extraction and coal mining lead to significant environmental pollution and health hazards [ 7 ]. While biopolymer alternatives derived from renewable resources are beginning to emerge for some polymer types [ 10 ], similar considerations as fossil carbon-based plastics may apply throughout the remainder of the life cycle. Fossil carbon-based derivatives from the petrochemical industry are also the basis for most chemicals used in plastic production. Other plastic chemicals, such as many catalysts in polymerisation reactions and certain functional additives rely on the extraction of various (heavy) metals. Heavy metal mining contaminates surrounding soil, farmland and water bodies, including ground water, which negatively impacts both the ecosystems and human health [ [11] , [12] , [13] ]. Fig. 1 The life cycle of plastic. The plastic life cycle involves four main stages: the extraction of raw materials, production and manufacturing, use/consumption, and disposal/waste management. Several steps are involved in production and manufacturing: 1) Monomer units are produced from the carbon feedstock; 2) Monomer units undergo polymerisation to produce polymers; 3) Polymers are compounded with additives to produce the desired material properties; and 4) this mixture is converted into the final plastic products. 5) Rubbers also undergo vulcanisation, which enhances their mechanical properties by causing the polymer chains to cross-link, forming a three-dimensional network structure. Fig. 1 The life cycle of plastic. The plastic life cycle involves four main stages: the extraction of raw materials, production and manufacturing, use/consumption, and disposal/waste management. Several steps are involved in production and manufacturing: 1) Monomer units are produced from the carbon feedstock; 2) Monomer units undergo polymerisation to produce polymers; 3) Polymers are compounded with additives to produce the desired material properties; and 4) this mixture is converted into the final plastic products. 5) Rubbers also undergo vulcanisation, which enhances their mechanical properties by causing the polymer chains to cross-link, forming a three-dimensional network structure. The second stage of the plastic life cycle, production and manufacturing , involves the transformation of carbon feedstocks into a range of plastic products. It relies heavily on fossil carbon derived from coal (67 %), petroleum (23 %) and natural gas (10 %), both as feedstock for monomer production and as fuel [ 14 ]. The scale of plastic production (460 Mt in 2019 [ 1 ]) and anticipated increases present serious issues regarding sustainability, as the use of fossil resources results in a myriad of climate, environmental and health externalities [ 15 ] such as greenhouse gas emissions and particulate matter (PM) air pollution [ 16 ]. Monomer units produced from the carbon feedstock then undergo polymerisation, facilitated by initiators, catalysts, and solvents, to produce polymers in granular or pellet form (also called nurdles) [ 7 ]. Next, additives are added to the polymers during the compounding process to produce the desired material properties such as colour, transparency, flexibility, and flame resistance [ 7 ]. During conversion, this mixture is converted into the final plastic products using various mechanical processes, often involving heat. An additional step involved in rubber production is vulcanisation which enhances the mechanical properties of the rubber by causing the polymer chains to cross-link, forming a three-dimensional network structure. At any step of the plastic production and manufacturing stage, additional chemicals such as processing aids are added to enable or ease production or processing of plastics [ 7 ]. Hazardous plastic-associated chemicals may be released during transportation and manufacture [ 17 ], posing significant risks to the environment and human health (e.g., vinyl chloride leakage and explosion [ 18 ]). Releases of hazardous chemicals are often concentrated in areas where other petrochemical production is occurring, thereby presenting disproportionate risks to nearby communities, known as fenceline communities, which are typically vulnerable populations [ 7 ]. Furthermore, plastic pellets – primary microplastics used for manufacturing plastic products – are released into the environment via factory run-off into drains, loss during transport/handling and via accidental spills during shipping. They can also leach hazardous chemicals such as polychlorinated biphenyls (PCBs) and polycyclic aromatic hydrocarbons (PAHs) into seawater [ 19 ], can act as vectors of environmental pollutants by adsorbing persistent organic pollutants (POPs) from the environment [ 20 , 21 ], and can act as a vector for pathogenic microorganisms such as E. coli and Vibrio species , including V. cholerae [ 22 , 23 ]. During use (or consumption [ 24 ] ) , the third stage of the plastic life cycle, plastic-associated chemicals and micro- and nanoplastics (MNPs) are sources of environmental contamination and human exposure [ 25 ]. There is leakage of monomers, oligomers, additives, and other chemicals present in plastic products with known or likely hazard, either individually or as hazardous chemical mixtures, into the environment. For example, phthalates, which are plasticisers added to plastics to provide flexibility, have been detected in water, air, and soil [ 26 ]. Humans are inevitably exposed to these chemicals from their surrounding environment, for example, via ingestion of contaminated drinking water or inhalation of contaminated air [ 27 ]. Similarly, degradation of plastic products during use (e.g., tyre abrasion, washing of textiles, and paint wear) lead to the release of secondary MNPs into the environment [ 1 ]. These secondary microplastics add to primary microplastic waste entering the environment such as from plastic microbead exfoliants in personal care products, with humans then being exposed to via ingestion or inhalation [ 7 , 28 ]. Importantly, MNPs have unknown safety [ 7 , 29 , 30 ]. Humans can also be exposed to plastic-associated chemicals and MNPs directly from product use, for example, via ingestion due to chemicals and MNPs migrating into food/drinks from food contact materials [ 8 , 31 , 32 ]. Disposal of plastic, the fourth and final stage of the plastic life cycle, also poses major environmental and human health challenges, which heavily depend on waste management processes [ 33 ]. In 2019, 353 out of the 460 Mt of plastic produced became waste. Of this waste, 50 % was landfilled, 19 % incinerated, and 9 % recycled [ 1 ]. The remaining 22 % was mismanaged, for example, through littering, uncontrolled dumpsites, accidental or uncontrolled fires including open burning, or leakage to the environment [ 34 ]. During disposal, there are several potential risks to environmental and human health due to leakage/release of hazardous monomers, polymers and plastic-associated chemicals, formation of MNPs from environmental degradation of plastic products, and greenhouse gas emissions from incineration/open burning, landfilling or dumping. Importantly, MNP pollution is likely to be transboundary [ 35 ]. Additionally, persistence and bioaccumulation (in the environment and in humans) of chemicals with potential to migrate from plastic materials are also of concern. Furthermore, plastic-associated chemicals may adversely impact the recyclability of plastic materials/products, and the safety of resulting materials [ 33 ]. Table 1 summarises environmental and human health impact factors of plastic-associated chemicals, polymers, and products throughout the life cycle of fossil carbon-based plastic [ 7 , 25 ] – extraction of raw materials, production and manufacturing, use (consumption) and disposal (waste management) [ 24 ]. Table 1 Examples of environmental and human health impact factors of plastic chemicals, polymers, and products/applications throughout the life cycle of fossil carbon-based plastic. Table 1 Impact factors Chemicals Polymer Application/product Extraction of raw materials Environmental impact factors Environmental release during extraction Environmental release of metals (e.g., for use as catalysts or stabilisers) from mining, leading to soil contamination and water pollution The estimated share of fossil carbon used in plastic production was 6 % in 2014 and is predicted to increase to 20 % by 2050 [ 36 ] Oil and gas extraction and coal mining lead to significant air pollution (e.g., particulate matter (PM), oxides of nitrogen (NO x ), oxides of sulphur (SO x )) and water pollution (e.g., benzene, toluene, ethylbenzene, and xylene (BTEX), metals, radioactive isotopes) Release of volatile hydrocarbons, leading to formation of ground-level ozone Greenhouse gas emissions during coal, gas and oil extraction (methane) Accidental oil spills Relevant to all applications/products Human health (safety) impact factors Occupational risks during extraction Heavy metal mining is a physically hazardous occupation with elevated risk of acute and chronic injury/disease and death Oil and gas extraction and coal mining are physically hazardous occupations with elevated risk of acute and chronic injury/disease and death Relevant to all applications/products Occupational and fenceline community exposure during extraction Occupational exposure during heavy metal mining and exposure in fenceline communities due to environmental release and contamination of farmland Exposure in workers and fenceline communities to hazardous chemicals (e.g., ozone and volatile organic compounds (VOCs) such as BTEX, formaldehyde) due to air pollution and contamination of drinking water Relevant to all applications/products Production & Manufacturing Environmental impact factors Greenhouse gases and climate impact Refinement of fossil feedstock to base chemicals including separation, conversion, and treatment [ 37 ] Production of additives and other chemicals used for plastic production Refinement of fossil feedstock to base chemicals including separation, conversion, and treatment Due to polymer feedstock (e.g., fossil carbon-based plastics) and energy use for plastic production Relevant to all applications/products Environmental release during production & manufacturing Environmental release of chemicals used in polymer production (e.g., solvents, catalysts) and plastic manufacture (e.g., additives) Environmental release of plastic pellets/nurdles (primary micro- and/or nanoplastics (MNPs)), hazardous monomers and by-products (e.g., bisphenol A (BPA) and oligomers during injection moulding of polycarbonate (PC)) Environmental release of hazardous chemicals which are application-specific during plastic manufacture (e.g., blowing agents for expanded polystyrene (EPS)) Human health (safety) impact factors Occupational exposure during production   & manufacturing Occupational exposure to chemicals used in polymer production (e.g., solvents, catalysts) and plastic manufacture (e.g., additives) Occupational exposure to hazardous monomers, VOCs, and by-products (e.g., vinyl chloride and hydrogen chloride respectively during manufacture of polyvinyl chloride (PVC)) Occupational exposure to hazardous chemicals which are application specific (e.g., plasticisers for plasticised/soft PVC) during plastic manufacture Fenceline community exposure during production & manufacturing Exposure to chemicals used in polymer production and plastic manufacture due to their emissions/releases into waste, air, water, and soil (e.g., additives and catalysts) Exposure to hazardous monomers, VOCs, and other by-products due to their emissions into waste, air, water, and soil Exposure to hazardous chemicals which are application specific (e.g., plasticisers for plasticised/soft PVC) due to their emissions/releases into waste, air, water, and soil Use (consumption) Environmental impact factors Known environmental release during use Most chemical additives and non-intentionally added substances (NIAS) in plastics are not covalently bound to the polymer matrix, and may migrate from plastic products (e.g., plasticisers and flame retardants) MNPs released during use (e.g., tyre abrasion) MNPs released during use of personal care products containing plastic microbeads Additional unintentional environmental release during use Potential for chemicals used in production to remain in final product (e.g., processing aids and catalysts) and migrate into the environment Potential for residual monomers and by-products, including polymer breakdown products, to remain in final product and migrate into the environment (e.g., BPA from PC) Potential for application-specific chemicals in the final product to migrate into the environment during use Potential for release of chemicals, NIAS and residual monomers during use due to application (e.g., heat or mechanical stress) Application-based degradation during use (e.g., PC contact with heat), leading to environmental release of breakdown products & MNPs Human health (safety) impact factors Human exposure during use Most chemical additives (e.g., plasticisers and flame retardants) and NIAS in plastics are not covalently bound to the polymer matrix, and therefore migrate from plastic products, leading to human exposure during use Potential for chemicals that were used in manufacture (e.g., processing aids and catalysts) to also remain in final product and migrate from plastic products Residual monomers and polymer breakdown products may be present in and migrate from plastic products (e.g., BPA from PC) Exposure to MNPs during use (e.g., PVC pipes) Applications whereby direct exposure to chemicals and polymer breakdown products occur, such as food contact materials and medical products (e.g., intravenous tubing) Exposure to hazardous chemicals which are application specific (e.g., plasticisers emitted into indoor environments from plasticised/soft PVC flooring) Potential for release of chemicals, NIAS, residual monomers and MNPs during use due to application, leading to exposure (e.g., release of BPA from PC container due to polymer degradation when exposed to heat [ 38 , 39 ] or acidic/alkaline solutions or use of detergents [ 40 ]) Disposal (waste management) Environmental impact factors Greenhouse gases and climate impact Emission of greenhouse gases, occurring with degradation in the environment, but especially due to incineration, and accidental or uncontrolled fires, such as landfill fires, house fires, backyard burning and burning for recycling other materials (e.g., PVC-insulated cables for copper retrieval) Energy use for all disposal and recycling methods Release of ozone depleting substances with high global warming potential (e.g., historical use of chlorofluorocarbons (CFCs) as blowing agents for EPS) End-of-life management such as transport of EPS Persistence Persistent and bio-accumulative potential of the chemicals in the environment (e.g., persistent organic pollutants (POPs)) Biodegradability of the polymer. Most fossil carbon-based polymers do not easily degrade in the environment/landfills Availability of end-of-life management options (e.g., tyres – issues with recycling, downcycling, landfilling & incineration) Landfilling Chemicals migrating from plastic products in landfills contaminate the air, soil, and groundwater, even long after the landfills are decommissioned Monomers/oligomers and MNPs formed due to degradation in landfills and potentially released into the environment via reuse of mineralised refuse Tyres can cause landfill instability, which can allow pollutants from other municipal waste to migrate into the environment Tyres are also a fire hazard (act as a fire propellant) and can be hazardous to human health by acting as a breeding ground for vector-borne illnesses Littering and mismanaged waste Chemicals, including additives and NIAS, migrate from plastic products, leading to environmental impacts Leakage of monomers/oligomers or as MNPs due to degradation in the environment Primary MNPs and other applications whereby there is a high likelihood for mismanaged waste/littering (e.g., single-use plastics such as cutlery and straws) Incineration Potential for release of hazardous pollutants (e.g., polybrominated dibenzo- p -dioxins and dibenzofurans (PBDD/Fs) produced as by-products of brominated flame retardants) into the environment from malfunctioning incinerator and/or depending on the scavenging methods used and whether optimal operation conditions are met Chemicals (e.g., heavy metals used as stabilisers) migrate from incineration residues which are landfilled or processed, resulting in both air and soil contamination Potential for release of hazardous pollutants (e.g., chlorine gas, polychlorinated dibenzodioxins and/or dibenzofurans (PCDD/Fs), hydrogen chloride) into the environment depending on the scavenging methods used and whether optimal operation conditions are met Relevant to all applications/products Recyclability   Not recyclable and/or hinder the recycling of other items Additives in plastic products are rarely recoverable for reuse (except via feedstock recycling, which is not currently scalable) Use of chemicals of concern (e.g., legacy POPs) in plastics hinders circularity of the products Additives added during recycling can also degrade the quality of recycled plastic due to incompatibility with additives already present in the product Halogenated polymers are less recyclable due to their intrinsic susceptibility to heat and they contaminate recycling streams, leading to release of hazardous chemicals (e.g., PVC) Use of polymer mixtures in production of plastic products affects recyclability of the product (e.g., cling films) Some plastic products (e.g., plastic films, soft plastics) are hard to recycle irrespective of the specific chemicals or polymers used to produce them Products made with a variety of materials (e.g., carton lined with plastic) are also harder to recycle Some polymers are not easy to recycle due to their application (e.g., EPS) By-products of recycling Dispersion of hazardous additives (e.g., flame retardants) and their transformation products (e.g., PBDD/Fs) into the broader environment during recycling When polymers are melted in an extruder during mechanical recycling, VOCs are formed as degradation products MNPs released into the environment during mechanical recycling Downcycling (e.g., tyres as crumbed rubber) increases the leakage of hazardous chemicals into the environment Human health (safety) impact factors Occupational exposure during collection and sorting Occupational exposure to hazardous additives (e.g., flame retardants) during collection and sorting Occupational exposure to monomers during collection and sorting (e.g., styrene when cutting foam boards) Application-specific occupational exposure to hazardous chemicals (e.g., waste pickers) Exposure due to landfilling Hazardous chemicals (e.g., additives) migrate from plastic products in landfills, contaminate the air, soil, and groundwater, even long after the landfills are decommissioned, leading to occupational exposure and exposure in fenceline communities Exposure to hazardous chemicals (e.g., hydrochloric acid from PVC degradation in landfills) migrating from plastic products in landfills and contaminating the air, soil, and groundwater, even long after the landfills are decommissioned Tyres can cause landfill instability, which can allow pollutants from other municipal waste to migrate into the environment, leading to human exposure Occupational and fenceline community exposure due to incineration Exposure in workers and fenceline communities to hazardous pollutants (e.g., PBDD/Fs produced as by-products of brominated flame retardants) due to their release from malfunctioning incinerator and/or depending on the scavenging methods used and whether optimal operation conditions are met Occupational exposure to hazardous monomers (e.g., BPA and bisphenol analogues from PC) during incineration Potential exposure in fenceline communities to hazardous pollutants such as PCDD/Fs due to their release from malfunctioning incinerator and/or depending on the scavenging methods used and whether optimal operation conditions are met Relevant to all applications/products Occupational exposure during recycling Occupational exposure in recycling workers to hazardous additives (e.g., flame retardants) and their transformation products (e.g., PBDD/Fs) Occupational exposure to hazardous by-products such as VOCs formed during the melting process of recycling (e.g., hydrochloric acid from PVC) and MNPs during recycling Application-specific occupational exposure to hazardous chemicals during recycling (e.g., informal e-waste recycling workers) Fenceline community exposure near recycling facilities Exposure to hazardous additives (e.g., flame retardants) and their transformation products (e.g., PBDD/Fs) due to their emissions/releases into waste, air, water, and soil Exposure to hazardous by-products (e.g., hydrochloric acid from PVC) and MNPs due to their emissions/releases into waste, air, water, and soil Application-specific exposure to hazardous chemicals due to their emissions/releases into waste, air, water, and soil (e.g., living close to e-waste recycling facilities) Recyclability Cannot safely be recycled with regard to hazardous content Use of chemicals of concern (e.g., legacy POPs) in plastics hinders safe circularity of the products Halogenated polymers contaminate recycling streams, leading to release of and exposure to hazardous chemicals (e.g., PVC) Potential for food safety issues with open-loop plastics Exposure via recycled products Recycled products contain higher concentrations of additives, leading to greater exposure levels Introduction of additional NIAS to recycled products due to contamination during disposal (e.g., metals and POPs adsorbed from the environment) Introduction of monomers/oligomers formed during melting process of recycling as NIAS to recycled plastic products Introduction of additional NIAS into recycled plastic due to application-specific contamination during use (e.g., chemicals from previously packaged food) Examples of environmental and human health impact factors of plastic chemicals, polymers, and products/applications throughout the life cycle of fossil carbon-based plastic. The impacts of plastic across its life cycle are dependent on the associated polymers, chemicals, and applications/products. As a result, it is imperative that policies and regulations aimed at mitigating the impacts of plastic on environmental and human health consider all three dimensions of plastics by looking at the plastic problem from each of the three lenses. While there are national and/or international regulations to phase out the use of hazardous chemicals and problematic plastic products, no global framework for identifying and regulating polymers of concern in plastics throughout their life cycle exists [ 3 , 5 , 41 , 42 ]. Although there have been several reviews on the impacts of plastic on environmental and human health, these mainly focus on the impacts associated with plastic-associated chemicals [ 7 , 43 , 44 ], MNPs [ 7 , 45 ], or specific applications of plastic [ 7 , 46 ]. Similarly, LCA studies are largely focused on human toxicity impacts from non-plastic specific exposure to chemical substances [ 47 ] or environmental sustainability issues of plastic products/specific plastic applications [ 48 ]. Importantly, LCA studies on plastic polymers typically focus on one or more focal areas of concern with the primary focus being on overall global warming potential, and the impacts associated with disposal scenarios [ 16 , [49] , [50] , [51] , [52] ]; with far less consideration of environmental/human exposure to the chemicals associated with the plastic polymers (e.g., processing aids, additives, NIAS) during production, use as well as disposal/recycling [ 53 , 54 ]. Furthermore, studies on the human health impacts of exposure to the polymers themselves have almost exclusively been conducted using skin patch tests [ 44 ]. This review provides a synthesis of scientific evidence on the impacts of plastic across its life cycle, viewed through a polymer lens and accounting for environmental release of and human exposure to plastic-associated chemicals and MNPs, including in product/application-specific situations, which will provide critical information for consideration in the negotiations for the Global Plastics Treaty, which aims to end plastic pollution by addressing all stages of its life cycle [ [55] , [56] , [57] , [58] ]. Plastic materials can be made of various polymers depending on the properties required such as strength, flexibility, resistance to corrosion, heat/electrical conductivity, transparency and cost. To examine the impacts of plastic from a polymer lens, four examples of problematic polymers were selected for this review. The prioritisation process considered the hazardous properties of monomers and their degree of migration from food contact plastics, the amount and hazardous properties of additives and particulates associated with the polymers, as well as the polymer type and uniquely pressing challenges associated with the processing of, or end-of-life management of, particular polymers. Specifically, the substances of potential concern list by Wiesinger and colleagues (2021) [ 4 ] was used to identify monomers which are known organic carcinogens, mutagens or reproductive toxicants with very high production volumes (>10 Mt per year) and are not regulated by any international convention. A total of 13 chemicals were identified from the list, namely BPA (CASRN: 80-05-7; monomer for polycarbonate (PC) and epoxy resins), styrene (CASRN: 100-42-5; monomer for polystyrene (PS), styrene acrylonitrile copolymer (SAN), acrylonitrile butadiene styrene (ABS), and styrene-butadiene rubber), vinyl chloride (CASRN: 75-01-4; monomer for polyvinyl chloride (PVC) and polyvinylidene chloride), 1,3-butadiene (CASRN: 106-99-0; monomer for polybutadiene, styrene-butadiene rubber, and ABS), ethanol (CASRN: 64-17-5; not a monomer), phenol (CASRN: 108-95-2; phenol-formaldehyde resin monomer), acrylonitrile (CASRN: 107-13-1; monomer for ABS, polyacrylonitrile (PAN), SAN), formaldehyde (CASRN: 50-00-0; monomer for phenol-formaldehyde resin, urea-formaldehyde resins, melamine-formaldehyde resins, and polyformaldehyde), methanol (CASRN: 67-56-1; not a monomer), propylene oxide (CASRN: 75-56-9; monomer for polypropylene glycol), ethylene glycol (CASRN: 107-21-1; monomer for polyethylene terephthalate (PET) and polyethylene glycol), vinyl acetate (CASRN: 108-05-4; monomer for polyvinyl acetate and polyvinyl alcohol), isobutylene (CASRN: 115-11-7; polyisobutylene monomer) [ 59 ]. The FCCmigex database [ 9 ] was then used to link the monomers identified above to polymers of concern with respect to their degree of migration from food contact plastics. Monomers BPA and styrene had the highest evidence of leaching/migration from plastic food contact materials with 191 and 109 database entries respectively compared to ≤31 for the other 11 chemicals. When grouped by material, PC and PS materials had the highest evidence of leaching their respective monomers (77 and 76 database entries respectively compared to ≤49 for the other nine known polymers included in the database). In addition to PC and PS, PVC was chosen for this review because the plasticisers diethylhexyl phthalate (DEHP, CASRN 117-81-7) and di- n -butyl phthalate (DnBP, CASRN 84-74-2) were the two most common food contact chemicals in plastics in the FCCmigex database. About 80 % of all plasticisers produced are used to make plasticised PVC (PPVC), with the typical amount being 10 % – 70 % weight/weight of PVC material [ 6 ]. Additionally, PVC is used in a range of consumer products such that human exposure to PVC-associated chemicals occurs via all exposure pathways [ 60 ]: inhalation (e.g., vinyl flooring [ 60 ]), ingestion (e.g., food contact materials [ 61 ]), dermal absorption (e.g., personal care products packaging [ 62 ]), and direct exposure (e.g., medical devices [ 63 ]). Moreover, PVC MNPs have shown the greatest particle toxicity (greatest increase in pro-inflammatory cytokine release) in primary human monocytes in vitro [ 64 ]. Importantly, this effect of polymer has been found to be independent of leached chemicals and particle size/shape, with an independent effect of leached chemicals and particle size/shape also demonstrated. Furthermore, chlorinated polymers like PVC pose unique challenges, including in end-of-life management, compared to other plastics [ 65 ]. Lastly, polybutadiene rubber was chosen due to impacts associated with the vulcanisation process and thermosetting resins (PC, PS and PVC are thermoplastics). Also, end-of-life management of tyres pose unique challenges, and road transport, in particular the wear of tyres and brake pads, is one of the main sources of microplastic pollution, with tyre abrasion accounting for 3 % of total mismanaged plastic waste and 25 % of total microplastic waste [ 34 ]. It is important to note that there are several other important polymers which may require additional considerations, not covered here by the four prioritised polymers. There is no established priority list of “problematic polymers” or “polymers of concern” and criteria and/or framework for identifying polymers of concern with respect to environmental and human health impacts are currently being proposed for the Treaty and other regulatory bodies [ 3 , 66 , 67 ]. Production volume and microplastic toxicity have been consistently proposed to be included in the criteria. It has been reported that 24 % of all plastics used in 2019 were made of polyethylene (PE), 16 % were made of polypropylene (PP), 5 % were made of PET, and 4 % were made of polyurethane (PUR) [ 34 ]. A recent study ranking polymers based on hazards of microplastics in the environment reported that PUR, PVC, PAN, ABS, poly(methyl methacrylate), SAN, thermoplastic polyurethanes, unsaturated polyester, PET, PS, and high-density PE were the top-ranking polymers of concern in descending order [ 68 ]. Another study evaluated the risk of harm from microplastics across the entire material life cycle and found that PVC, PP and PS had the highest cumulative risk ranking [ 67 ]. Polyamine (e.g., nylon) is also considered an important polymer of concern due to evidence of hazardous impacts of inhaled microfibers [ 7 ]. Despite the common occurrence of these polymers in the environment and their relevance for consideration, they were beyond the scope of this review due to our prioritisation process, which places more emphasis on unavoidable issues inherent to the polymer such as hazardous properties of monomers and additives, their migration from food packaging, and end-of-life processing. This review focuses on four examples of common polymers made from hazardous monomers: PCs made from bisphenols, PS made from styrene, PVC made from vinyl chloride, and polybutadiene made from 1,3-butadiene. The main objective of this review is to identify and compile evidence of environmental leakage, human exposure, and health impacts associated with PC, PS, PVC, and polybutadiene across their life cycle, with regards to the chemicals and processes used to produce them and the additives commonly incorporated to achieve the properties needed for applications for which the polymers are generally used. For each polymer, we have provided the type of polymer (thermoplastic vs thermoset), the properties of the polymer, its common uses/applications, production volume and percentage of total plastic production, the different types of polymers within the category and their differences (where applicable), information on alternatives (where applicable), and a table compiling extensive evidence of environmental leakage, human exposure, and health impacts associated with the polymer. The table contains information on the life cycle stages and sub-stages (see Fig. 1 ) to which the plastic pollutants and their impacts are associated with, and the plastic pollutants relevant for each stage/sub-stage, including monomers, oligomers, additives, processing aids, NIAS, PM, and MNPs. Chemical classes and/or specific chemicals are listed and the functions of all known intentionally added substances are provided, along with hazard information on specific plastic-associated chemicals obtained from Wiesinger and colleagues (2021) [ 4 ], the International Agency for Research on Cancer (IARC) Classified Agents List [ 69 ], the Substance of Very High Concern (SVHC) list by the Registration, Evaluation, Authorisation and Restriction of Chemicals (REACH) [ 70 ], the ChemSec Substitute it Now (SIN) list [ 71 ], and the list of persistent, bioaccumulative and toxic (PBT) substances in the Stockholm Convention [ 72 ]. Evidence of environmental leakage, human exposure, and health impacts for each pollutant/group of pollutants/chemical class at each stage/sub-stage are summarised. Lastly, information on alternatives for the polymer, chemical, or product is provided, where relevant, and we have noted how their environmental and human health impacts differ. The CAS registration number and hazard classification of the specific chemicals identified within this review are provided in the Supplementary Material (Excel Tables S1–S5 ). Hazard classifications were obtained from Wiesinger and colleagues (2021) [ 4 ], in which chemicals with “high level of concern” were defined as substances that have a production volume of ≥1000 metric tons per year and fulfil one or more of the following hazard criteria under EU REACH: PBT/very persistent and very bioaccumulative, carcinogenicity, mutagenicity, reproductive toxicity, specific target organ toxicity upon repeated exposure, chronic aquatic toxicity, respiratory sensitisation, and endocrine disruption. Overall, this review demonstrates important considerations, in addition to the hazardous properties of constituent monomers, when evaluating/prioritising ‘problematic’ polymers. This review is therefore broadly relevant to scientists, policy makers and other stakeholders involved in the development of criteria for polymer assessment and management across the globe.

The authors declare that they have no known competing financial interests or personal relationships that could have appeared to influence the work reported in this paper.

Polybutadiene is a thermosetting plastic known for its high flexibility, tensile strength, and resistance to abrasion. It is predominantly used in the manufacture of tyres, specifically the treads and sidewalls [ 275 ]. Polybutadiene (estimated to constitute around 30 % of the synthetic polymers used in tyres) [ 276 ], along with other synthetic polymers, comprise approximately 24 % of a passenger or light truck tyre and 11 % of a truck tyre [ 277 ]. Other applications of polybutadiene include footwear, sporting equipment (e.g., golf ball cores), conveyor belts, and cable insulation [ 278 ]. Polybutadiene may also be added to other polymers, such as PS and ABS, where it is used as a toughening agent [ 275 ]. The annual global market volume for polybutadiene was 3.99 Mt in 2019 [ 279 ], accounting for 0.87 % of total plastic production [ 1 ]. As a thermoset material, and because of the chemical composition and hazardous properties of constituent materials, vulcanised polybutadiene tyres cannot be recycled via simple mechanical recycling [ 280 ]. Used tyres can instead be retreaded [ 281 ] or downcycled for use as crumbed/ground rubber in playgrounds and sports facilities [ 282 ] or used in other applications [ [283] , [284] , [285] ]. There are a range of potential alternatives to polybutadiene across its numerous applications. Biodegradable and photodegradable alternatives include utilisation of polybutadiene composites with biodegradable polymers such as co-polymers of polybutadiene and polylactic acid (PLA) [ 286 ]. Polybutadiene alternatives for use in tyres include natural rubber , though scalability may be a challenge, and degradable PLA co-polymers of elastomers [ 287 ], which also present environmental and health concerns. Table 5 outlines the environmental leakage and human exposure, or health impacts associated with polybutadiene, particularly in the context of a synthetic tyre rubber, throughout its life cycle. Table 5 Environmental leakage and human health impact factors of polybutadiene throughout its life cycle, particularly in the context of synthetic tyre rubber. Table 5 Life cycle stage Plastic pollutants Environmental leakage and/or human exposure/health impacts Extraction of raw materials Extraction of fossil resources – for fossil carbon Greenhouse gases, particulate matter (PM), metal(loid)s, volatile organic compounds (VOCs) such as benzene, toluene, ethylbenzene, and xylene [ 7 ] Emitted during plastic production, transport and/or end-of-life processes [ 7 ], leading to climate, environmental and health impacts [ 14 , 15 ]. Alternatives: Bio-polybutadiene derived from renewable resources such as sugarcane or corn is being investigated as an alternative [ 288 ]. Bio-polybutadiene otherwise still requires similar considerations as fossil carbon-based polybutadiene materials for the rest of their life cycle as detailed below. Production & Manufacturing Monomer production & Polymerisation Butadiene – monomer A known human carcinogen [ 289 ] and one of the top air pollution-related health risk drivers in the United States [ 290 ] – documented release of butadiene into the atmosphere during production [ 291 ] and polymerisation [ 292 ], leading to occupational exposure [ 293 ] and detectable level of butadiene in drinking and ground water [ 294 ]. Products of degradation and atmospheric reactions of butadiene (e.g., 1,3-butadiene monoxide and 1,3-butadiene diepoxide) are considered more carcinogenic than butadiene itself [ 295 ]. Polymerisation Titanium tetrachloride – catalyst Shows specific target organ toxicity upon repeated exposure [ 4 ]. Chronic occupational exposure associated with lung diseases [ 296 ]. Low environmental exposure risk due to their rapid breakdown in the environment [ 296 ]. Compounding Carbon black – UV stabiliser and reinforcing filler in tyres Shows specific target organ toxicity upon repeated exposure [ 4 ] (known lung irritant) – occupational exposure increases the risk of chronic inflammatory and fibrotic lung diseases, such as pneumoconiosis [ 297 ]. Benzophenone-type UV stabilisers Potential for occupational exposure, which can lead to adverse human health effects, including altered kidney function [ 298 , 299 ] and increased risk of osteoarthritis [ 300 ]. Vulcanisation VOCs and semi-VOCs (e.g., benzene, hydrazine, and n-Nitrosodi- n -propylamine) Benzene, hydrazine, and n-Nitrosodi- n -propylamine are carcinogens [ 4 ] on the ChemSec Substitute it Now (SIN) list [ 71 ]. Occupational exposure associated with higher risk of cancer [ 301 , 302 ]. Polycyclic aromatic hydrocarbons (PAHs) Carcinogenic [ 303 ] – occupational exposure documented [ 302 ]. Use (consumption) Tyre wear particles – secondary micro- and/or nanoplastics (MNPs) Released into the environment [ 304 , 305 ] and a major source of MNP in air and water [ 1 ] – leachates are hazardous [ [306] , [307] , [308] , [309] ] and can contain PAHs and metals such as zinc, lead, cadmium [ 309 , 310 ]. N-(1,3-dimethylbutyl)-N′-phenyl- p -phenylenediamine (6PPD) stabiliser Migrates from tyre wear particles and transforms into 6PPD-quinone, causing aquatic toxicity [ 311 , 312 ] and potentially affect human health based on animal studies showing multi-organ toxicity [ 313 ]. Disposal (waste management) Landfilling Whole tyres Tyres can cause landfill instability, which can allow pollutants from other municipal waste to migrate into the environment [ 314 , 315 ]. Tyre leachate can contaminate soil, groundwater and surface water [ 314 ]. The synthetic components of tyres do not biodegrade and therefore, accumulate in landfills which have limits for the amount of tyres they can accept [ 314 , 315 ]. Alternatives: A biodegradable alternative include utilisation of polylactic acid (PLA) co-polymers of elastomers [ 287 ]. Accidental or uncontrolled fires, e.g., landfill fires and burning of scrap tyres PM, carbon monoxide, SO x , NO x , VOCs, benzene, PAHs, polychlorinated dibenzodioxins and/or dibenzofurans (PCDD/Fs), and polychlorinated biphenyls (PCBs), and some trace elements such as arsenic, cadmium, nickel, zinc, mercury, chromium, vanadium Hazardous pollutants [ 4 ] released into the air and aquatic environment [ 314 , 316 , 317 ], leading to serious threat to the environment [ 315 ], human exposure and potential health risks [ 318 , 319 ]. Tyre-derived fuel PM, carbon monoxide, SO x , NO x , PAHs, PCDD/Fs, metals such as zinc Potentially released into the environment [ [320] , [321] , [322] ], leading to environmental and human health impacts. Recycling/downcycling for use as crumbed rubber PAHs and metals such as zinc, lead, and cobalt Migrate into the environment [ 323 , 324 ] and may impact marine life [ [324] , [325] , [326] ] and human health [ 327 ]. Environmental leakage and human health impact factors of polybutadiene throughout its life cycle, particularly in the context of synthetic tyre rubber.

PC is a thermoplastic polymer with good thermal resistance, mechanical properties, durability, and high optical transparency, making it suitable for a range of commodities and for engineering applications in construction, automotive, aircraft, data storage, electrical, and telecommunication hardware [ 73 ]. The annual global demand for PC was 4.6 Mt in 2019 [ 74 ], accounting for 1 % of total plastic production [ 1 ]. PC resins can be divided into two structural classes based on their carbon chain backbone: aliphatic and aromatic PCs. The main differences between the chemical structures of the aliphatic and aromatic PCs are due to the different types of monomers used in their synthesis. Aliphatic PCs have backbones of repeating carbonate (- O –C(O)– O -) linkages, while aromatic PCs are formed when the carbonate group is directly connected to an aromatic carbon [ 75 ]. There are no aromatic groups between the carbonate linkages for the aliphatic PCs [ 75 ]. These structural differences mainly influence the physicochemical properties and degradability of PCs [ 75 ]. • Aliphatic PCs consist of non-aromatic (aliphatic) repeating units and are generally biodegradable. Due to their aliphatic chemical structure, they are generally more flexible with lower glass transition temperature and more biocompatibility than aromatic PCs [ 76 ]. This makes aliphatic PCs more suitable for biomedical and pharmaceutical applications [ [76] , [77] , [78] ]. • Aromatic PCs consist of aromatic repeating units. Their structure results in higher glass transition temperatures, more heat resistance and higher rigidity in comparison with the aliphatic PCs [ 75 ]. Higher mechanical and thermal stabilities of aromatic PCs make them more suitable for electrical and automotive industry [ 75 ]. Aromatic PCs are used to make thermoplastics. The most important and widely used aromatic PC is poly (bisphenol A) carbonate [ 79 , 80 ]. Regulatory bans and restrictions placed on BPA use have led to its substitution with BPA analogues, such as bisphenol S (BPS) and bisphenol F (BPF) [ 81 ]. These substitute chemicals are likely to present similar health risks [ [82] , [83] , [84] ], being structurally similar, but human biomonitoring data are currently sparse [ 84 , 85 ]. Aliphatic PCs consist of non-aromatic (aliphatic) repeating units and are generally biodegradable. Due to their aliphatic chemical structure, they are generally more flexible with lower glass transition temperature and more biocompatibility than aromatic PCs [ 76 ]. This makes aliphatic PCs more suitable for biomedical and pharmaceutical applications [ [76] , [77] , [78] ]. Aromatic PCs consist of aromatic repeating units. Their structure results in higher glass transition temperatures, more heat resistance and higher rigidity in comparison with the aliphatic PCs [ 75 ]. Higher mechanical and thermal stabilities of aromatic PCs make them more suitable for electrical and automotive industry [ 75 ]. Aromatic PCs are used to make thermoplastics. The most important and widely used aromatic PC is poly (bisphenol A) carbonate [ 79 , 80 ]. Regulatory bans and restrictions placed on BPA use have led to its substitution with BPA analogues, such as bisphenol S (BPS) and bisphenol F (BPF) [ 81 ]. These substitute chemicals are likely to present similar health risks [ [82] , [83] , [84] ], being structurally similar, but human biomonitoring data are currently sparse [ 84 , 85 ]. While aliphatic and aromatic PCs have distinct properties, there are some applications where both types of PCs can be used interchangeably or where their properties overlap, e.g., electronics, automotive parts. Nevertheless, aliphatic PCs cannot be used as an alternative to aromatic PCs for most applications. Table 2 outlines the life cycle of PCs, providing insights into the pollutants associated with each stage, along with their environmental leakage and human exposure or health impacts. Table 2 Environmental leakage and human health impact factors of polycarbonate (PC) throughout its life cycle. Table 2 Life cycle stage Plastic pollutants Environmental leakage and/or human exposure/health impacts Extraction of raw materials Extraction of fossil resources – for fossil carbon Greenhouse gases, particulate matter, metal(loid)s, volatile organic compounds such as benzene, toluene, ethylbenzene, and xylene [ 7 ] Emitted during plastic production, transport and/or end-of-life processes [ 7 ], leading to climate, environmental and health impacts [ 14 , 15 ]. Alternatives: Bio-based PCs are derived from carbon dioxide and renewable feedstocks such as plant oils, industrial by-products (crude glycerol) and pure fatty acids [ 86 ]. Bio-based PCs require similar considerations as fossil carbon-based PCs across the rest of their life cycle as detailed below. Some bio-based PCs may be aromatic bio-PCs [ 87 ] and others may be aliphatic bio-PCs [ 88 ], which have added end-of-life options such as enhanced biodegradability [ 89 ]. Nevertheless, similar to fossil carbon-based PCs, aliphatic and aromatic bio-PCs have distinct properties and while there can be overlaps in application, aliphatic bio-PCs cannot be used as an alternative for aromatic bio-PCs for most applications. Production & Manufacturing Monomer production, Polymerisation & Conversion Phosgene - used in polymerisation of bisphenols to aromatic PCs Highly toxic and corrosive [ 90 ] reproductive toxicant [ 4 ] – leaks in chemical facilities [ 91 , 92 ]. Methylene chloride (CH 2 Cl 2 ) – polymerisation solvent A carcinogenic, mutagenic, reproductive toxicant [ 4 ] – occupational exposure linked to increased risk of cancer [ 93 ]. Bisphenol A (BPA) and bisphenol analogues - monomer BPA is an endocrine disruptor [ 4 ] with several known health impacts, including increased risk of cardiometabolic disorders [ 94 , 95 ], polycystic ovary syndrome [ 96 ], type 2 diabetes [ 97 , 98 ], and obesity [ [99] , [100] , [101] ]. Potential emissions from BPA manufacturing facilities, during transport or during processing of BPA [ 80 ]. BPA is released in the indoor atmosphere [ 102 ], leading to occupational exposure [ 85 , 103 ]. Alternatives: BPA-free aromatic PCs can be made with bisphenol analogues such as BPS and BPF, which may have similar health effects [ [82] , [83] , [84] ]. Some bio-based PCs may be BPA-free [ 87 ], in particular, aliphatic bio-PCs do not contain BPA or bisphenol analogues [ 88 ]. Use (consumption) BPA and bisphenol analogues Migrates from the PC products leading to dietary exposure [ 80 , 104 , 105 ], transdermal exposure [ 106 ] or inhalation exposure via BPA in air and dust [ 107 ]. See health impacts above. Non-intentionally added substances (NIAS) Several NIAS such as oligomers and other PC-degradation products migrate from PC products [ 8 , 9 , 108 ] – potential for human exposure and unknown safety. Disposal (waste management) Landfilling BPA and bisphenol analogues Release and/or migrate from PC at environmental temperatures and normal pH in landfills [ 80 ]. Micro- and/or nanoplastics (MNPs) Formed due to PC degradation, potential release into the environment via reuse of mineralised refuse [ 109 ]. Littering and mismanaged waste BPA and bisphenol analogues Released into the environment due to PC degradation [ 110 , 111 ] – detected in fresh fish tissues and seafood, which affects humans via the food chain [ 112 ]. MNPs Released into the environment due to PC degradation [ 80 ]. MNPs have unknown safety [ 7 ]. Incineration BPA and bisphenol analogues Occupational exposure with subsequent health risks [ 113 , 114 ]. Recycling PC products are usually not accepted in curbside collection, but drop-off and special collection services exist. Collected PC products can be mechanically recycled or depolymerized [ 115 , 116 ]. Environmental leakage and human health impact factors of polycarbonate (PC) throughout its life cycle.

No data was used for the research described in the article.