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Review

A Review of Polychlorinated Biphenyls (PCBs) Pollution in the Air: Where and How Much Are We Exposed to?

by
Naffisah Othman
1,
Zaliha Ismail
1,*,
Mohamad Ikhsan Selamat
1,
Siti Hamimah Sheikh Abdul Kadir
2 and
Nur Amirah Shibraumalisi
3
1
Department of Public Health Medicine, Faculty of Medicine, Universiti Teknologi MARA Sungai Buloh Campus, Jalan Hospital, Sungai Buloh 47000, Malaysia
2
Department of Biochemistry, Faculty of Medicine, Universiti Teknologi MARA Sungai Buloh Campus, Jalan Hospital, Sungai Buloh 47000, Malaysia
3
Department of Primary Care Medicine, Faculty of Medicine, Universiti Teknologi MARA Sungai Buloh Campus, Jalan Hospital, Sungai Buloh 47000, Malaysia
*
Author to whom correspondence should be addressed.
Int. J. Environ. Res. Public Health 2022, 19(21), 13923; https://doi.org/10.3390/ijerph192113923
Submission received: 14 September 2022 / Revised: 13 October 2022 / Accepted: 19 October 2022 / Published: 26 October 2022
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Abstract

:
Polychlorinated biphenyls (PCBs) were widely used in industrial and commercial applications, until they were banned in the late 1970s as a result of their significant environmental pollution. PCBs in the environment gained scientific interest because of their persistence and the potential threats they pose to humans. Traditionally, human exposure to PCBs was linked to dietary ingestion. Inhalational exposure to these contaminants is often overlooked. This review discusses the occurrence and distribution of PCBs in environmental matrices and their associated health impacts. Severe PCB contamination levels have been reported in e-waste recycling areas. The occurrence of high PCB levels, notably in urban and industrial areas, might result from extensive PCB use and intensive human activity. Furthermore, PCB contamination in the indoor environment is ten-fold higher than outdoors, which may present expose risk for humans through the inhalation of contaminated air or through the ingestion of dust. In such settings, the inhalation route may contribute significantly to PCB exposure. The data on human health effects due to PCB inhalation are scarce. More epidemiological studies should be performed to investigate the inhalation dose and response mechanism and to evaluate the health risks. Further studies should also evaluate the health impact of prolonged low-concentration PCB exposure.

1. Introduction

Polychlorinated biphenyls (PCBs) are a group of toxic environmental pollutants categorized as persistent organic pollutants (POPs). The commercial production of PCBs started in 1929. Their main use was in electrical and hydraulic equipment and construction materials. Because of their significant adverse effects on human well-being and ecosystems, the manufacturing of PCBs was banned in the United States in 1979 under the US Toxic Substance Control Act [1]. Nevertheless, production continued elsewhere. As a result, the Stockholm Convention was established by the United Nations Environment Programme in May 2001, with the aim of eliminating PCB-containing products by 2028 in an environmentally sound manner [2]. Following this effort, the international total ban of PCBs came into effect on 17 May 2004.
There is still a long way to go, as only 3 million tons of PCB products had been eliminated as of 2015. Meanwhile, 80% of PCBs (17 million tons) are still in the environment, highlighting that the risk of exposure has not yet been eliminated [3]. Even with the production of PCBs banned in most countries, they continue to pose a threat due to their environmental persistence and bioaccumulation, raising global concerns. PCBs are still slowly and continuously being released by products that were manufactured before the ban and that are dumped as waste into the environment [4,5]. They are found in the ambient air and the food chain, and can be transmitted to humans through the ingestion of contaminated food products, inhalation, or transdermal exposure. PCBs have been detected in various food samples, and human exposure has been reported in several countries worldwide [6,7,8].

2. Polychlorinated Biphenyls (PCBs)

Polychlorinated biphenyls (PCBs) are a group of synthetic aromatic chemicals. They consist of a biphenyl structure that is bound to hydrogen and chlorine atoms according to the chemical formula C12HxCly, where x and y range from 1 to 10, and x + y = 10. The chemical structure of chlorinated biphenyls is shown in Figure 1. According to IUPAC, there are 209 PCB congeners, which differ by the number of hydrogen atoms substituted by chlorine atoms and their position on the biphenyl rings. This variance in PCB molecule determines the physical and chemical properties and toxicity.
The phenyl rings can rotate around the C-C bond, but with an increasing number of chlorines in the ortho positions (2, 2, 6, 6), this rotation is hampered. With no ortho-chlorines, the two phenyls can align co-planarly [9]. The plane between the phenyls as the C-C bond attain increased double bond characteristics is stabilized by the aromatic system. However, with an increased number of chlorine atoms in the ortho position, the likelihood that planarity will be established decreases. This is significant for the toxicity of the individual congener, as the toxicity of co-planar non-ortho congeners have a “dioxin-like” toxicity [10]. Mono-ortho congeners may also be somewhat co-planar, but if there are two or more chlorines in the ortho position, co-planarity is not possible.

3. Why Concern about PCBs

PCBs are among the 12 initial POPs called the “dirty dozen” under the Stockholm Convention [11], listed in Annex A (elimination) and Annex C (unintentional production). They are of global concern due to their (1) persistence in the environment, (2) long-distance travel in the atmosphere, (3) bioaccumulation, and (4) biomagnification in the food chain. It is a global issue, as everyone is likely to have some amount of PCB in their body from either the ingestion of contaminated food, inhalation, or dermal exposure to a polluted environment. Thus, PCBs can significantly impact animal and human health and the environment.
The consumption of contaminated food is often regarded as the major source of human PCB exposure, and there have been limited studies on the role of air pollution as an inhalational pathway. Because of the high PCB concentrations in some animals, dietary exposure has traditionally been prioritized in studies over dermal and inhalation exposure. However, the inhalation route of PCB exposure is often overlooked. A study reported decreased PCB concentrations in food, highlighting that inhalation may be an essential route of exposure [12]. Airborne emissions of PCB may result in inhalation exposure levels comparable to, and occasionally more significant than, dietary ingestion [13].
Atmospheric PCB is a significant contributor to the total body burden, as evidenced by elevated blood levels of lower-chlorinated PCBs (dominant congeners) in the air by 40% among occupants of contaminated buildings [14]. For people living in buildings with significant PCB levels in the building materials, the bulk of their overall PCB burden comes from exposures in their homes, nearly 40 years after the Danish ban on the use of PCBs in construction products [15]. Following exposure, PCB can bioaccumulate and persist in the human body for up to 12 years [16]. Many lower-chlorinated congeners are likewise endocrine-disruptive [17] and carcinogenic [18]. This indicates that inhalation and dermal absorption are significant routes of exposure to PCBs in the air [19]. This review discussed the occurrence of PCBs in the air as a source of inhalation exposure and the subsequent impacts on human health in light of the increased interest in this study area.

4. Occurrence of PCBs in the Air

The primary source of PCBs in the atmosphere is the volatilization of PCB-containing products in landfills that are disposed of as waste [20,21]. The widespread use of PCBs in commercial and industrial products and their inappropriate disposal have created severe environmental contamination. Today, PCBs can still be released into the environment from the following sources: (1) poorly maintained hazardous waste sites that contain PCBs; (2) illegal or improper dumping of PCB wastes into landfills that are not designed to handle hazardous waste; (3) accidental spills and leaks during the transport of the chemical; (4) leaks or fires from electrical transformers, capacitors, or other products containing PCBs; and (5) waste incineration and open burning in landfills that emit PCBs during the combustion process [1].
Once in the environment, PCBs do not readily break down. Instead, they undergo chemical biotransformation that allow them to continue cycling between air, water, and soil for an extended period. PCBs in the air are generally lower-chlorinated (≤5 chlorine atoms), and are mainly taken up by humans via inhalation and dermal resorption. In contrast to high-chlorinated congeners (>5 chlorine atoms), lower chlorinated PCBs exhibit a faster elimination rate from the body and a lower environmental persistence. Figure 2 shows the sources of PCB in the air, human exposure and possible health impacts.

4.1. Outdoor Environments

Despite the restricted use of PCBs for nearly four decades, PCB residues have been found in various environmental matrices across the globe. Interestingly, the concentrations of PCBs vary seasonally: they are higher in the soil during winter and higher in the air during summer [22]. This seasonal variation suggests that the emission of PCBs from the soil increases during hot seasons due to volatilization, especially low-chlorinated PCBs. The standards and regulations are designed for the occurrence of PCBs in the environment to protect humans from probable adverse health effects by the U.S. government (Table S1) [23].

4.1.1. E-Waste Recycling Areas

The atmosphere has a significant impact on the long-term transformation and distribution of POPs, including PCBs. The emission sources of PCBs in the environment have seen a shift from intentionally produced PCBs to a combination of intentionally and unintentionally produced and e-waste [24]. In areas where severe PCB pollution in the atmosphere has been reported, burning and recycling of electrical and electronic waste (e-waste) have become a primary source. In the course of recycling e-waste, processes such as manual dismantling, shredding, roasting printed circuit boards, acid-stripping metals, and open burning of e-waste can release these contaminants as unintended by-products [25]. The amount of PCB released to the environment can differ depending on the type of e-waste and the operating technique. High temperatures utilized during the disassembly process can lead to significantly higher PCB releases into the atmosphere. The highest concentration of PCBs were detected in heating furnaces and incinerators in shops working on televisions and hard disks [26].
Similar to other POPs, the peak concentrations of PCBs in the atmosphere can be attributed to emissions from the uncontrolled burning of solid waste, which contaminates surrounding areas [27]. A high concentration of atmospheric PCB has been reported in e-waste disassembling areas in both southern [28] and northern China [29]. In South Asia, the PCB concentration in the surface soil near informal e-waste recycling sites was approximately 23-fold higher than in open dumpsites [30]. Exposure to PCB near e-waste sites is closely related to hormone disruption, especially in children [31]. Furthermore, high PCB concentrations were reported in the blood of e-waste workers following occupational exposure [32,33] and individuals living near e-waste recycling plants [34]. These findings imply that simple e-waste disassembly processes could also be a significant source of PCB emissions.
With effective waste management becoming increasingly challenging, municipal solid waste incineration (MSWI) has emerged as an alternative in developed countries. Even though MSWI is aimed at recovering energy and reducing volume, it has been linked to the emissions of heavy metals and toxic chemicals, along with volatile organic compounds and polyaromatic hydrocarbons, which pose a threat of cancerous and non-cancerous diseases among the nearby population [35,36]. Recent studies have shown that municipal solid waste incinerators are among the most significant contributors to environmental pollutants. The authors of [20] reported decreasing atmospheric PCB levels with increasing the distance from the emission source.

4.1.2. Industrial Areas

PCBs have been widely used in industries over the decades. They can be released through industrial processes such as smelting and cooking, as well as during the burning of coal, wood, crude oil, gasoline, and diesel fuel [37,38]. PCBs in the atmosphere have been detected at higher levels in industrial areas, which are mainly produced unintentionally [39].
Atmospheric PCBs can be found in gaseous or particulate phases. They can bind to particulate matter and be distributed as fine particles due to their low vapor pressure [40]. In Germany, significant gaseous emissions of PCBs were detected from a silicone rubber production site, which was urged to take mitigation measures [41]. In highly industrialized areas, the incidence of chronic illness is likely to grow in parallel with economic growth, with increases in lifestyle diseases and the abundance of carcinogens in the environment [42].
PCBs in the air can be carried long distances and have been reported in regions with no industrial activity, where they have never been used [43]. Consequently, they are found worldwide, although the concentrations might be lower with increased distance from the emission source [20]. The occurrence and homologous patterns of PCBs in the environment can vary depending on chemical volatility, ambient temperature, topography, atmospheric transport, and soil organic matter content, which will predict the potential health risks of human exposure.

4.1.3. Urban vs. Rural Area

Because of the source and usage, PCB concentrations in the air are significantly higher in industrial and urban areas than in remote areas [21,44]. According to Ampleman, Martinez [45], the level of PCB exposure via inhalation is relatively higher among urban than rural residents. With more than half of the world’s population living in urban areas, this risk is worrying.
A clear demarcation of the concentration and occurrence of PCBs is seen between rural, urban, and industrial areas. The PCB concentrations in industrial areas are two to five times higher than in rural areas; in Chile’s urban and industrial areas, high-chlorinated congeners predominate [46]. On the other hand, lower-chlorinated PCBs predominates in the ambient air in Bursa Province [47] and Kutahya, a province in Turkey with a power plant [37]. Greater atmospheric PCB levels are typically observed in megalopolises with significant populations, such as in China [48].
In the United States, the PCB concentration in urban schools close to a PCB-contaminated waterway of Lake Michigan was significantly higher than in schools in rural areas. In fact, the concentration was higher in the indoor environment [49]. In remote areas, much lower atmospheric concentrations of PCB have been recorded. Monitoring of the spatial pattern and temporal trends of PCB at 16 background sites in the Tibetan Plateau showed concentrations ranging from 0.10 to 3.90 pg/m3 [50]. The concentrations and dominant congener profiles are summarized in Table 1.

4.2. Indoor Environments

While the concentrations of PCBs in the environment can be attributable to various sources, the indoor concentrations significantly exceed those in outdoor air [63]. This highlights that PCBs used and released indoors are more persistent and impact human health, as people spend most of their time indoors.

4.2.1. Building Design

The application of PCBs in construction has led to significant indoor air contamination in buildings [64]. PCBs were primarily used in construction materials such as plasticizers, paint, ceiling tiles, insulation, fluorescent lighting, caulk, and roofing from the 1950s to the late 1970s [65,66,67,68].
As a result of their inert property, PCBs are still present in such materials in homes and schools and will remain there for centuries. In Denmark, the concentration of PCBs in houses was seven-fold higher (2330 ng PCBtotal/m3) than the lowest action level (300 ng PCBtotal/m3) recommended by the Danish Health Authority [69]. This indicates that possible PCB exposure in the indoor environment contributes to significant overall PCB exposure among the Danish population [14]. With lifetime exposure, the health effects might be more significant. Meanwhile, routine air monitoring in a public building in Aachen, Germany, revealed considerable contamination due to prior use of PCBs in elastic joint sealants, particularly lower-chlorinated PCBs [19].
Aside from building construction, the concentration of indoor PCBs are significantly influenced by the ratio of wall and ceiling area to building volume. Additionally, contaminated air can be absorbed by a tertiary product such as a sealant, which will contribute significantly to the total indoor PCB concentration. Indoor PCB levels were found to be lower in residences with a larger total amount of sealant per volume ratio [70]. Additionally, the interior design of a building can determine the indoor PCB concentration. Carpet pads and wood floor finishes can be residential sources of these semi-volatile organic compounds, as they tend to partition to non-mobile household surfaces [71].
Indoor PCBs are semi-volatile and are slowly but continuously released into the air. Therefore, they can evaporate from their sources and subsequently absorb into surfaces, including dust and bioaccumulate in humans via inhalation and non-dietary ingestion [72,73]. PCBs have been found in dust from homes and other indoor environments worldwide. Indoor exposure to PCBs in contaminated buildings can occur via air and dust inhalation and dust ingestion [49,74]. The inhalation of PCBs from contaminated indoor air may lead to significant PCB levels in the blood [75]. Table 2 shows the concentration and dominant congeners in indoor environments in different settings.

4.2.2. Dust Ingestion

In addition to direct human exposure to PCBs through inhalation, airborne PCBs can contaminate indoor dust, which potentially impacts human health via unintentional ingestion. For example, a study conducted among 26 sample pairings in the United States found that PCBs in vacuum-cleaner dust were positively correlated with the levels of PCBs in human serum [91]. Furthermore, Frederiksen, Andersen [74] reported that residents of buildings constructed with PCB-containing materials that had significant dust PCB levels had high serum PCB levels.
While industrial emissions contribute as the major source of PCBs in urban areas, substantial dust pollution in rural houses poses significant exposure to this pollutant [81]. Approximately a quarter of non-dietary PCB exposure occurs through unintentional dust ingestion, especially among vulnerable groups [92]. In children, an increased risk of childhood leukemia has been linked to higher PCB levels in household dust [93]. At the same time, exposure to PCBs among older adults may contribute to a diminished cognitive ability [94].
For those who live in densely populated, developed regions and areas in proximity to industrial sources of PCBs, the exposure risk is higher in outdoor and indoor settings. In addition to direct exposure, indoor PCB contamination is likely influenced by the occurrence of PCBs in the outdoor air [79]. Similarly, the air in houses with backyard e-waste recycling has two to three times the PCB contamination than indoor air in urban areas [87]. Therefore, all sources of airborne PCBs should be considered when assessing PCB concentrations in indoor air [86].

5. Health Impact

PCBs pose a health risk to humans through three routes of exposure (oral ingestion, inhalation, and dermal absorption). While dietary consumption represents a major route of exposure in adults, inhalation presents a two times higher carcinogenic risk, especially among children [86]. In 2015, PCBs were classified as a Group 1 carcinogen (carcinogenic to humans) by the International Agency for Research on Cancer, which further highlights the significance of their oncogenic effects, and makes them a major toxicological concern across the globe [95].
Lerro, Jones [18] described a potential association between PBC exposure and thyroid cancer. PCBs are also proven to be a weakly estrogenic organic compound associated with testicular [96], prostate [97], and breast [98] cancer. In fact, PCB exposure can contribute to cancer aggressiveness and metastasis in women with breast cancer, worsening their prognosis [99]. In a population-based case-control study in the United States in 2005, higher chlorinated PCBs were associated with an increased risk of non-Hodgkin’s lymphoma [100]. Additionally, exposure to PCBs is also associated with the development of colorectal cancer [101], which was the second most common cause of cancer death worldwide in 2020 [102]. Overall, the risk of cancer is 20% higher in men with exposure to PCB [103].
Besides the carcinogenic risk, PCB exposure is also linked to various metabolic diseases. Evidence shows that PCB leads to insulin resistance, which in turn increases the risk of metabolic disorders [104,105,106]. Numerous studies have examined the association between plasma PCB levels and cardiovascular disease risk factors such as hypertension, type 2 diabetes, obesity, and dyslipidemia [107,108,109]. Concerning the health of future generations, studies on the association of serum PCB levels of pregnant women and pregnancy outcomes have shown a significant association with the neonatal thyroid hormone status [110,111]. The effects on infants might be due to in utero exposure [110,112] or breastmilk consumption [113,114,115].

6. Conclusions

Inhalation is an essential route of PCB exposure in humans. In this review, we considered scientific papers on environmental PCB contamination. In particular, we discussed the occurrence of PCBs in both outdoor and indoor air and related adverse effects on human health. E-waste recycling is the primary source of PCB contamination in the environment. This phenomenon indicates the need for a remediation strategy to protect the ecosystem from the threat of environmental pollutants.
We emphasized that studies in the literature have reported high PCB concentrations in indoor environments (including in air and dust) originating from building materials (furniture, paints, caulking compounds, and sealants), posing a threat to human health. There is limited knowledge on the available mitigation strategies to reduce PCB levels in the air. Common remediation methods for PCBs in building materials, such as source removal, chemical treatment, and encapsulation of the source, may redistribute the compounds to secondary sources (interior surfaces), causing widespread contamination. Therefore, research should focus on strategies that could help in decreasing high air concentrations of PCBs, especially in indoor environments. With effective mitigation strategies, the effort to eliminate these toxic organic compounds can be accelerated.
Further studies should evaluate PCB risks from inhalation exposure and its dose–response relationship. As it might be disregarded, additional research is needed to assess the health effects of sustained low-concentration PCB exposure.

Supplementary Materials

The following supporting information can be downloaded at: https://www.mdpi.com/article/10.3390/ijerph192113923/s1, Table S1: Standards and regulations for environmental standards of PCBs.

Funding

This study is funded by the Fundamental Research Grant Scheme (FRGS)-RACER, grant code: 600-IRMI/FRGS-RACER 5/3 (094/2019).

Institutional Review Board Statement

Not applicable as the review approach consisted of reviewing and gathering data from publicly available materials.

Informed Consent Statement

Not applicable.

Data Availability Statement

Not applicable.

Acknowledgments

This review is part of the postgraduate student’s thesis write-up.

Conflicts of Interest

The authors declare no conflict of interest.

References

  1. US EPA. Polychlorinated Biphenyls (PCBs). Available online: https://www.epa.gov/pcbs/learn-about-polychlorinated-biphenyls-pcbs (accessed on 18 October 2021).
  2. UNEP. PCB a Forgotten Legacy? Available online: https://www.unep.org/explore-topics/chemicals-waste/what-we-do/persistent-organic-pollutants/pcb-forgotten-legacy (accessed on 18 October 2021).
  3. Stockholm Convention. PCB Overview. Available online: http://chm.pops.int/Implementation/IndustrialPOPs/PCB/Overview/tabid/273/Default.aspx (accessed on 18 October 2021).
  4. Yu, H.; Liu, Y.; Shu, X.; Ma, L.; Pan, Y. Assessment of the spatial distribution of organochlorine pesticides (OCPs) and polychlorinated biphenyls (PCBs) in urban soil of China. Chemosphere 2020, 243, 125392. [Google Scholar] [CrossRef] [PubMed]
  5. Peng, Y.; Wu, J.; Luo, X.; Zhang, X.; Giesy, J.P.; Mai, B. Spatial distribution and hazard of halogenated flame retardants and polychlorinated biphenyls to common kingfisher (Alcedo atthis) from a region of South China affected by electronic waste recycling. Environ. Int. 2019, 130, 104952. [Google Scholar] [CrossRef] [PubMed]
  6. Harmouche-Karaki, M.; Mahfouz, Y.; Salameh, P.; Matta, J.; Helou, K.; Narbonne, J.F. Patterns of PCBs and OCPs exposure in a sample of Lebanese adults: The role of diet and physical activity. Environ. Res. 2019, 179 Pt B, 108789. [Google Scholar] [CrossRef]
  7. Ravenscroft, J.; Schell, L.M. Patterns of PCB exposure among Akwesasne adolescents: The role of dietary and inhalation pathways. Environ. Int. 2018, 121 Pt 1, 963–972. [Google Scholar] [CrossRef] [PubMed]
  8. Rusin, M.; Dziubanek, G.; Marchwinska-Wyrwal, E.; Cwielag-Drabek, M.; Razzaghi, M.; Piekut, A. PCDDs, PCDFs and PCBs in locally produced foods as health risk factors in Silesia Province, Poland. Ecotoxicol. Environ. Saf. 2019, 172, 128–135. [Google Scholar] [CrossRef] [PubMed]
  9. ATSDR. Toxicological Profile for Polychlorinated Biphenyls (PCBs); ATSDR: Atlanta, GA, USA, 2014. [Google Scholar]
  10. ATSDR. Polychlorinated Biphenyls (PCBs) Toxicity; ATSDR: Atlanta, GA, USA, 2014. [Google Scholar]
  11. UNEP. Toward Elimination of PCB. Available online: https://www.unep.org/explore-topics/chemicals-waste/what-we-do/persistent-organic-pollutants/toward-elimination-pcb? (accessed on 18 October 2021).
  12. Saktrakulkla, P.; Lan, T.; Hua, J.; Marek, R.F.; Thorne, P.S.; Hornbuckle, K.C. Polychlorinated Biphenyls in Food. Environ. Sci. Technol. 2020, 54, 11443–11452. [Google Scholar] [CrossRef] [PubMed]
  13. Norstrom, K.; Czub, G.; McLachlan, M.S.; Hu, D.; Thorne, P.S.; Hornbuckle, K.C. External exposure and bioaccumulation of PCBs in humans living in a contaminated urban environment. Environ. Int. 2010, 36, 855–861. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  14. Egsmose, E.L.; Bräuner, E.V.; Frederiksen, M.; Mørck, T.A.; Siersma, V.D.; Hansen, P.W.; Nielsen, F.; Grandjean, P.; Knudsen, L.E. Associations between plasma concentrations of PCB 28 and possible indoor exposure sources in Danish school children and mothers. Environ. Int. 2016, 87, 13–19. [Google Scholar] [CrossRef]
  15. Meyer, H.W.; Frederiksen, M.; Goen, T.; Ebbehoj, N.E.; Gunnarsen, L.; Brauer, C.; Kolarik, B.; Muller, J.; Jacobsen, P. Plasma polychlorinated biphenyls in residents of 91 PCB-contaminated and 108 non-contaminated dwellings-an exposure study. Int. J. Hyg. Environ. Health 2013, 216, 755–762. [Google Scholar] [CrossRef] [PubMed]
  16. Esser, A.; Ziegler, P.; Kaifie, A.; Kraus, T.; Schettgen, T. Estimating plasma half-lives of dioxin like and non-dioxin like polychlorinated biphenyls after occupational exposure in the German HELPcB cohort. Int. J. Hyg. Environ. Health 2021, 232, 113667. [Google Scholar] [CrossRef] [PubMed]
  17. Aminov, Z.; Haase, R.; Rej, R.; Schymura, M.J.; Santiago-Rivera, A.; Morse, G.; DeCaprio, A.; Carpenter, D.O. Diabetes Prevalence in Relation to Serum Concentrations of Polychlorinated Biphenyl (PCB) Congener Groups and Three Chlorinated Pesticides in a Native American Population. Environ. Health Perspect. 2016, 124, 1376–1383. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  18. Lerro, C.C.; Jones, R.R.; Langseth, H.; Grimsrud, T.K.; Engel, L.S.; Sjodin, A.; Choo-Wosoba, H.; Albert, P.; Ward, M.H. A nested case-control study of polychlorinated biphenyls, organochlorine pesticides, and thyroid cancer in the Janus Serum Bank cohort. Environ. Res. 2018, 165, 125–132. [Google Scholar] [CrossRef] [PubMed]
  19. Schettgen, T.; Alt, A.; Preim, D.; Keller, D.; Kraus, T. Biological monitoring of indoor-exposure to dioxin-like and non-dioxin-like polychlorinated biphenyls (PCB) in a public building. Toxicol. Lett. 2012, 213, 116–121. [Google Scholar] [CrossRef]
  20. Li, M.; Zhou, Y.; Wang, G.; Zhu, G.; Zhou, X.; Gong, H.; Sun, J.; Wang, L.; Jinsong, L. Evaluation of atmospheric sources of PCDD/Fs, PCBs and PBDEs around an MSWI plant using active and passive air samplers. Chemosphere 2021, 274, 129685. [Google Scholar] [CrossRef] [PubMed]
  21. Zhu, M.; Yuan, Y.; Yin, H.; Guo, Z.; Wei, X.; Qi, X.; Liu, H.; Dang, Z. Environmental contamination and human exposure of polychlorinated biphenyls (PCBs) in China: A review. Sci. Total Environ. 2021, 805, 150270. [Google Scholar] [CrossRef]
  22. Barbas, B.; de la Torre, A.; Sanz, P.; Navarro, I.; Artinano, B.; Martinez, M.A. Gas/particle partitioning and particle size distribution of PCDD/Fs and PCBs in urban ambient air. Sci. Total Environ. 2018, 624, 170–179. [Google Scholar] [CrossRef]
  23. ATDSR. What Standards and Regulations Exist for PCB Exposure? Available online: https://www.atsdr.cdc.gov/csem/polychlorinated-biphenyls/standards.html (accessed on 25 August 2022).
  24. Cui, S.; Fu, Q.; Li, Y.F.; Li, T.X.; Liu, D.; Dong, W.C.; Wanga, M.; Li, L.Y. Spatial–temporal variations, possible sources and soil–air exchange of polychlorinated biphenyls in urban environments in China. RSC Adv. 2017, 7, 14797–14804. [Google Scholar] [CrossRef] [Green Version]
  25. Wong, M.H.; Wu, S.C.; Deng, W.J.; Yu, X.Z.; Luo, Q.; Leung, A.O.W.; Wong, C.S.C.; Luksemburg, W.J.; Wong, A.S. Export of toxic chemicals—A review of the case of uncontrolled electronic-waste recycling. Environ. Pollut. 2007, 149, 131–140. [Google Scholar] [CrossRef] [Green Version]
  26. Liu, R.; Ma, S.; Li, G.; Yu, Y.; An, T. Comparing pollution patterns and human exposure to atmospheric PBDEs and PCBs emitted from different e-waste dismantling processes. J. Hazard. Mater. 2019, 369, 142–149. [Google Scholar] [CrossRef]
  27. Wang, Y.; Luo, C.; Wang, S.; Cheng, Z.; Li, J.; Zhang, G. The Abandoned E-Waste Recycling Site Continued to Act As a Significant Source of Polychlorinated Biphenyls: An in Situ Assessment Using Fugacity Samplers. Environ. Sci. Technol. 2016, 50, 8623–8630. [Google Scholar] [CrossRef]
  28. Chen, S.-J.; Tian, M.; Zheng, J.; Zhu, Z.-C.; Luo, Y.; Luo, X.-J.; Mai, B.-X. Elevated Levels of Polychlorinated Biphenyls in Plants, Air, and Soils at an E-Waste Site in Southern China and Enantioselective Biotransformation of Chiral PCBs in Plants. Environ. Sci. Technol. 2014, 48, 3847–3855. [Google Scholar] [CrossRef] [PubMed]
  29. Hong, W.-J.; Jia, H.; Ding, Y.; Li, W.-L.; Li, Y.-F. Polychlorinated biphenyls (PCBs) and halogenated flame retardants (HFRs) in multi-matrices from an electronic waste (e-waste) recycling site in Northern China. J. Mater. Cycles Waste Manag. 2018, 20, 80–90. [Google Scholar] [CrossRef]
  30. Chakraborty, P.; Selvaraj, S.; Nakamura, M.; Prithiviraj, B.; Cincinelli, A.; Bang, J.J. PCBs and PCDD/Fs in soil from informal e-waste recycling sites and open dumpsites in India: Levels, congener profiles and health risk assessment. Sci. Total Environ. 2018, 621, 930–938. [Google Scholar] [CrossRef] [PubMed]
  31. Xu, P.; Lou, X.; Ding, G.; Shen, H.; Wu, L.; Chen, Z.; Han, J.; Han, G.; Wang, X. Association of PCB, PBDE and PCDD/F body burdens with hormone levels for children in an e-waste dismantling area of Zhejiang Province, China. Sci. Total Environ. 2014, 499, 55–61. [Google Scholar] [CrossRef]
  32. Kaifie, A.; Schettgen, T.; Bertram, J.; Lohndorf, K.; Waldschmidt, S.; Felten, M.K.; Kraus, T.; Fobil, J.N.; Kupper, T. Informal e-waste recycling and plasma levels of non-dioxin-like polychlorinated biphenyls (NDL-PCBs)—A cross-sectional study at Agbogbloshie, Ghana. Sci. Total Environ. 2020, 723, 138073. [Google Scholar] [CrossRef]
  33. Ma, S.; Ren, G.; Zeng, X.; Yu, Z.; Sheng, G.; Fu, J. Polychlorinated biphenyls and their hydroxylated metabolites in the serum of e-waste dismantling workers from eastern China. Environ. Geochem. Health 2018, 40, 1931–1940. [Google Scholar] [CrossRef] [PubMed]
  34. Dai, Q.; Xu, X.; Eskenazi, B.; Asante, K.A.; Chen, A.; Fobil, J.; Bergman, A.; Brennan, L.; Sly, P.D.; Nnorom, I.C.; et al. Severe dioxin-like compound (DLC) contamination in e-waste recycling areas: An under-recognized threat to local health. Environ. Int. 2020, 139, 105731. [Google Scholar] [CrossRef] [PubMed]
  35. Domingo, J.L.; Rovira, J.; Nadal, M.; Schuhmacher, M. High cancer risks by exposure to PCDD/Fs in the neighborhood of an Integrated Waste Management Facility. Sci. Total Environ. 2017, 607–608, 63–68. [Google Scholar] [CrossRef]
  36. Wang, H.; Hao, R.; Nie, L.; Zhang, X.; Zhang, Y. Pollution characteristics and risk assessment of air multi-pollutants from typical e-waste dismantling activities. Environ. Pollut. 2022, 294, 118630. [Google Scholar] [CrossRef]
  37. Dumanoglu, Y.; Gaga, E.O.; Gungormus, E.; Sofuoglu, S.C.; Odabasi, M. Spatial and seasonal variations, sources, air-soil exchange, and carcinogenic risk assessment for PAHs and PCBs in air and soil of Kutahya, Turkey, the province of thermal power plants. Sci. Total Environ. 2017, 580, 920–935. [Google Scholar] [CrossRef]
  38. Hao, Y.; Li, Y.; Han, X.; Wang, T.; Yang, R.; Wang, P.; Xiao, K.; Li, W.; Lu, H.; Fu, J.; et al. Air monitoring of polychlorinated biphenyls, polybrominated diphenyl ethers and organochlorine pesticides in West Antarctica during 2011-2017: Concentrations, temporal trends and potential sources. Environ. Pollut. 2019, 249, 381–389. [Google Scholar] [CrossRef] [PubMed]
  39. Hu, J.; Zheng, M.; Liu, W.; Nie, Z.; Li, C.; Liu, G.; Xiao, K. Characterization of polychlorinated dibenzo-p-dioxins and dibenzofurans, dioxin-like polychlorinated biphenyls, and polychlorinated naphthalenes in the environment surrounding secondary copper and aluminum metallurgical facilities in China. Environ. Pollut. 2014, 193, 6–12. [Google Scholar] [CrossRef] [PubMed]
  40. Yang, X.; Wu, J.; Li, M.; Qi, M.; Wang, R.; Hu, J.; Jin, J. Particle size distributions and health risks of polychlorinated dibenzo-p-dioxin/furans, polychlorinated biphenyls, and polychlorinated naphthalenes in atmospheric particles around two secondary copper smelters in Shandong Province, China. Chemosphere 2021, 269, 128742. [Google Scholar] [CrossRef] [PubMed]
  41. Hombrecher, K.; Quass, U.; Leisner, J.; Wichert, M. Significant release of unintentionally produced non-Aroclor polychlorinated biphenyl (PCB) congeners PCB 47, PCB 51 and PCB 68 from a silicone rubber production site in North Rhine-Westphalia, Germany. Chemosphere 2021, 285, 131449. [Google Scholar] [CrossRef]
  42. Cetin, B.; Yurdakul, S.; Keles, M.; Celik, I.; Ozturk, F.; Dogan, C. Atmospheric concentrations, distributions and air-soil exchange tendencies of PAHs and PCBs in a heavily industrialized area in Kocaeli, Turkey. Chemosphere 2017, 183, 69–79. [Google Scholar] [CrossRef]
  43. Eckhardt, S.; Breivik, K.; Mano, S.; Stohl, A. Record high peaks in PCB concentrations in the Arctic atmosphere due to long-range transport of biomass burning emissions. Atmos. Chem. Phys. 2007, 7, 4527–4536. [Google Scholar] [CrossRef] [Green Version]
  44. Qu, C.; Albanese, S.; Lima, A.; Hope, D.; Pond, P.; Fortelli, A.; Romano, N.; Cerino, P.; Pizzolante, A.; De Vivo, B. The occurrence of OCPs, PCBs, and PAHs in the soil, air, and bulk deposition of the Naples metropolitan area, southern Italy: Implications for sources and environmental processes. Environ. Int. 2019, 124, 89–97. [Google Scholar] [CrossRef]
  45. Ampleman, M.D.; Martinez, A.; DeWall, J.; Rawn, D.F.; Hornbuckle, K.C.; Thorne, P.S. Inhalation and dietary exposure to PCBs in urban and rural cohorts via congener-specific measurements. Environ. Sci. Technol. 2015, 49, 1156–1164. [Google Scholar] [CrossRef] [Green Version]
  46. Pozo, K.; Harner, T.; Rudolph, A.; Oyola, G.; Estellano, V.H.; Ahumada-Rudolph, R.; Garrido, M.; Pozo, K.; Mabilia, R.; Focardi, S. Survey of persistent organic pollutants (POPs) and polycyclic aromatic hydrocarbons (PAHs) in the atmosphere of rural, urban and industrial areas of Concepción, Chile, using passive air samplers. Atmos. Pollut. Res. 2012, 3, 426–434. [Google Scholar] [CrossRef] [Green Version]
  47. Birgül, A.; Kurt-Karakus, P.B.; Alegria, H.; Gungormus, E.; Celik, H.; Cicek, T.; Güven, E.C. Polyurethane foam (PUF) disk passive samplers derived polychlorinated biphenyls (PCBs) concentrations in the ambient air of Bursa-Turkey: Spatial and temporal variations and health risk assessment. Chemosphere 2017, 168, 1345–1355. [Google Scholar] [CrossRef]
  48. Wang, P.; Zhang, Q.; Li, Y.; Matsiko, J.; Zhang, Y.; Jiang, G. Airborne persistent toxic substances (PTSs) in China: Occurrence and its implication associated with air pollution. Environ. Sci. Process Impacts 2017, 19, 983–999. [Google Scholar] [CrossRef] [PubMed]
  49. Marek, R.F.; Thorne, P.S.; Herkert, N.J.; Awad, A.M.; Hornbuckle, K.C. Airborne PCBs and OH-PCBs Inside and Outside Urban and Rural U.S. Schools. Environ. Sci. Technol. 2017, 51, 7853–7860. [Google Scholar] [CrossRef]
  50. Wang, X.; Ren, J.; Gong, P.; Wang, C.; Xue, Y.; Yao, T.; Lohmann, R. Spatial distribution of the persistent organic pollutants across the Tibetan Plateau and its linkage with the climate systems: A 5-year air monitoring study. Atmos. Chem. Phys. 2016, 16, 6901–6911. [Google Scholar] [CrossRef] [Green Version]
  51. Miglioranza, K.S.B.; Ondarza, P.M.; Costa, P.G.; de Azevedo, A.; Gonzalez, M.; Shimabukuro, V.M.; Grondona, S.I.; Mitton, F.M.; Barra, R.O.; Wania, F.; et al. Spatial and temporal distribution of Persistent Organic Pollutants and current use pesticides in the atmosphere of Argentinean Patagonia. Chemosphere 2021, 266, 129015. [Google Scholar] [CrossRef] [PubMed]
  52. Bartlett, P.W.; Isaksson, E.; Hermanson, M.H. ‘New’ unintentionally produced PCBs in the Arctic. Emerg. Contam. 2019, 5, 9–14. [Google Scholar] [CrossRef]
  53. Mila, A.; Cao, R.; Geng, N.; Zhu, X.; Chen, J. Characteristics of PAHs, PCDD/Fs, PCBs and PCNs in atmospheric fine particulate matter in Dalian, China. Chemosphere 2022, 288, 132488. [Google Scholar] [CrossRef]
  54. Mi, H.-H.; Wu, Z.-S.; Lin, L.-F.; Lai, Y.-C.; Lee, Y.-Y.; Wang, L.-C.; Chang-Chien, G.-P. Atmospheric Dry Deposition of Polychlorinated Dibenzo-p-Dioxins/Dibenzofurans (PCDD/Fs) and Polychlorinated Biphenyls (PCBs) in Southern Taiwan. Aerosol Air Qual. Res. 2012, 12, 1016–1029. [Google Scholar] [CrossRef] [Green Version]
  55. Xu, C.; Niu, L.; Zou, D.; Zhu, S.; Liu, W. Congener-specific composition of polychlorinated biphenyls (PCBs) in soil-air partitioning and the associated health risks. Sci. Total Environ. 2019, 684, 486–495. [Google Scholar] [CrossRef] [PubMed]
  56. Lopez, A.; Coscolla, C.; Hernandez, C.S.; Pardo, O.; Yusa, V. Dioxins and dioxin-like PCBs in the ambient air of the Valencian Region (Spain): Levels, human exposure, and risk assessment. Chemosphere 2021, 267, 128902. [Google Scholar] [CrossRef]
  57. Kurt-Karakusa, P.B.; Ugranli-Cicek, T.; Sofuoglu, S.C.; Celik, H.; Gungormus, E.; Gedik, K.; Sofuoglu, A.; Okten, H.E.; Birgul, A.; Alegria, H.; et al. The first countrywide monitoring of selected POPs: Polychlorinated biphenyls (PCBs), polybrominated diphenyl ethers (PBDEs) and selected organochlorine pesticides (OCPs) in the atmosphere of Turkey. Atmos. Environ. 2018, 177, 154–165. [Google Scholar] [CrossRef]
  58. Cetin, B.; Yurdakul, S.; Gungormus, E.; Ozturk, F.; Sofuoglu, S.C. Source apportionment and carcinogenic risk assessment of passive air sampler-derived PAHs and PCBs in a heavily industrialized region. Sci. Total Environ. 2018, 633, 30–41. [Google Scholar] [CrossRef]
  59. Fang, M.; Choi, S.-D.; Baek, S.-Y.; Jin, G.; Chang, Y.-S. Deposition of polychlorinated biphenyls and polybrominated diphenyl ethers in the vicinity of a steel manufacturing plant. Atmos. Environ. 2012, 49, 206–211. [Google Scholar] [CrossRef]
  60. Aydin, Y.M.; Kara, M.; Dumanoglu, Y.; Odabasi, M.; Elbir, T. Source apportionment of polycyclic aromatic hydrocarbons (PAHs) and polychlorinated biphenyls (PCBs) in ambient air of an industrial region in Turkey. Atmos. Environ. 2014, 97, 271–285. [Google Scholar] [CrossRef]
  61. Wang, Y.; Hu, J.; Lin, W.; Wang, N.; Li, C.; Luo, P.; Hashmi, M.Z.; Wang, W.; Su, X.; Chen, C.; et al. Health risk assessment of migrant workers’ exposure to polychlorinated biphenyls in air and dust in an e-waste recycling area in China: Indication for a new wealth gap in environmental rights. Environ. Int. 2016, 87, 33–41. [Google Scholar] [CrossRef]
  62. Chakraborty, P.; Prithiviraj, B.; Selvaraj, S.; Kumar, B. Polychlorinated biphenyls in settled dust from informal electronic waste recycling workshops and nearby highways in urban centers and suburban industrial roadsides of Chennai city, India: Levels, congener profiles and exposure assessment. Sci. Total Environ. 2016, 573, 1413–1421. [Google Scholar] [CrossRef]
  63. Sari, M.F.; Esen, F.; Del Aguila, D.A.C.; Karakus, P.B.K. Passive sampler derived polychlorinated biphenyls (PCBs) in indoor and outdoor air in Bursa, Turkey: Levels and an assessment of human exposure via inhalation. Atmos. Pollut. Res. 2020, 11, 71–80. [Google Scholar] [CrossRef]
  64. Audy, O.; Melymuk, L.; Venier, M.; Vojta, S.; Becanova, J.; Romanak, K.; Vykoukalova, M.; Prokes, R.; Kukucka, P.; Diamond, M.L.; et al. PCBs and organochlorine pesticides in indoor environments—A comparison of indoor contamination in Canada and Czech Republic. Chemosphere 2018, 206, 622–631. [Google Scholar] [CrossRef]
  65. Langeland, M.; Jensen, M.K. Kortlægning Af Pcb I Materialer Og Indelu: Fase 2 Rapport; Miljøstyrelsen: Odense, Denmark, 2013. [Google Scholar]
  66. US EPA. PCBs in Building Materials—Questions & Answers; US EPA: Washington, DC, USA, 2015. [Google Scholar]
  67. Herrick, R.F.; McClean, M.D.; Meeker, J.D.; Baxter, L.K.; Weymouth, G.A. An unrecognized source of PCB contamination in schools and other buildings. Environ. Health Perspect 2004, 112, 1051–1053. [Google Scholar] [CrossRef] [Green Version]
  68. Hellman, S.; Cajal, P.; Martinez, P.; Kuusisto, S.; Tuhkanen, T. PCB-contamination in a school building indoors. WIT Trans. Ecol. Environ. 2010, 129, 619–627. [Google Scholar] [CrossRef] [Green Version]
  69. Andersen, H.V.; Gunnarsen, L.; Knudsen, L.E.; Frederiksen, M. PCB in air, dust and surface wipes in 73 Danish homes. Int. J. Hyg. Environ. Health 2020, 229, 113429. [Google Scholar] [CrossRef]
  70. Kolarik, B.; Frederiksen, M.; Meyer, H.W.; Ebbehoj, N.E.; Gunnarsen, L.B. Investigation of the importance of tertiary contamination, temperature and human behaviour on PCB concentrations in indoor air. Indoor Built Environ. 2014, 25, 229–241. [Google Scholar] [CrossRef] [Green Version]
  71. Whitehead, T.P.; Brown, F.R.; Metayer, C.; Park, J.S.; Does, M.; Dhaliwal, J.; Petreas, M.X.; Buffler, P.A.; Rappaport, S.M. Polychlorinated biphenyls in residential dust: Sources of variability. Environ. Sci. Technol. 2014, 48, 157–164. [Google Scholar] [CrossRef] [Green Version]
  72. Andersen, H.V.; Frederiksen, M. Sorption of PCB from air to settled house dust in a contaminated indoor environment. Chemosphere 2021, 266, 129139. [Google Scholar] [CrossRef]
  73. Liu, X.; Guo, Z.; Krebs, K.A.; Greenwell, D.J.; Roache, N.F.; Stinson, R.A.; Nardin, J.A.; Pope, R.H. Laboratory study of PCB transport from primary sources to settled dust. Chemosphere 2016, 149, 62–69. [Google Scholar] [CrossRef]
  74. Frederiksen, M.; Andersen, H.V.; Haug, L.S.; Thomsen, C.; Broadwell, S.L.; Egsmose, E.L.; Kolarik, B.; Gunnarsen, L.; Knudsen, L.E. PCB in serum and hand wipes from exposed residents living in contaminated high-rise apartment buildings and a reference group. Int. J. Hyg. Environ. Health 2020, 224, 113430. [Google Scholar] [CrossRef]
  75. Kraft, M.; Rauchfuss, K.; Fromme, H.; Grun, L.; Sievering, S.; Kollner, B.; Chovolou, Y. Inhalation Exposure to PCB from Contaminated Indoor Air—How Much Is Absorbed into the Blood? Pollutants 2021, 1, 181–193. [Google Scholar] [CrossRef]
  76. Kang, Y.; Yin, Y.; Man, Y.; Li, L.; Zhang, Q.; Zeng, L.; Luo, J.; Wong, M.H. Bioaccessibility of polychlorinated biphenyls in workplace dust and its implication for risk assessment. Chemosphere 2013, 93, 924–930. [Google Scholar] [CrossRef]
  77. Iwegbue, C.M.A.; Eyengho, S.B.; Egobueze, F.E.; Odali, E.W.; Tesi, G.O.; Nwajei, G.E.; Martincigh, B.S. Polybrominated diphenyl ethers and polychlorinated biphenyls in indoor dust from electronic repair workshops in southern Nigeria: Implications for onsite human exposure. Sci. Total Environ. 2019, 671, 914–927. [Google Scholar] [CrossRef]
  78. Abafe, O.A.; Martincigh, B.S. An assessment of polybrominated diphenyl ethers and polychlorinated biphenyls in the indoor dust of e-waste recycling facilities in South Africa: Implications for occupational exposure. Environ. Sci. Pollut. Res. 2015, 22, 14078–14086. [Google Scholar] [CrossRef]
  79. Moreau-Guigon, E.; Alliot, F.; Gasperi, J.; Blanchard, M.; Teil, M.J.; Mandin, C.; Chevreuil, M. Seasonal fate and gas/particle partitioning of semi-volatile organic compounds in indoor and outdoor air. Atmos. Environ. 2016, 147, 423–433. [Google Scholar] [CrossRef]
  80. Anh, H.Q.; Watanabe, I.; Minh, T.B.; Tue, N.M.; Tuyen, L.H.; Viet, P.H.; Takahashi, S. Polychlorinated biphenyls in settled dusts from an end-of-life vehicle processing area and normal house dusts in northern Vietnam: Occurrence, potential sources, and risk assessment. Sci. Total Environ. 2020, 728, 138823. [Google Scholar] [CrossRef]
  81. Chandra Yadav, I.; Devi, N.L.; Li, J.; Zhang, G. Polychlorinated biphenyls and organochlorines pesticides in indoor dust: An exploration of sources and health exposure risk in a rural area (Kopawa) of Nepal. Ecotoxicol. Environ. Saf. 2020, 195, 110376. [Google Scholar] [CrossRef] [PubMed]
  82. Melymuk, L.; Bohlin-Nizzetto, P.; Kukucka, P.; Vojta, S.; Kalina, J.; Cupr, P.; Klanova, J. Seasonality and indoor/outdoor relationships of flame retardants and PCBs in residential air. Environ. Pollut. 2016, 218, 392–401. [Google Scholar] [CrossRef] [PubMed]
  83. de la Torre, A.; Sanz, P.; Navarro, I.; Martinez, M.d.L.A. Investigating the presence of emerging and legacy POPs in European domestic air. Sci. Total Environ. 2020, 746, 141348. [Google Scholar] [CrossRef]
  84. Frederiksen, M.; Meyer, H.W.; Ebbehoj, N.E.; Gunnarsen, L. Polychlorinated biphenyls (PCBs) in indoor air originating from sealants in contaminated and uncontaminated apartments within the same housing estate. Chemosphere 2012, 89, 473–479. [Google Scholar] [CrossRef]
  85. Besis, A.; Botsaropoulou, E.; Balla, D.; Voutsa, D.; Samara, C. Toxic organic pollutants in Greek house dust: Implications for human exposure and health risk. Chemosphere 2021, 284, 131318. [Google Scholar] [CrossRef]
  86. Aslam, I.; Baqar, M.; Qadir, A.; Mumtaz, M.; Li, J.; Zhang, G. Polychlorinated biphenyls in indoor dust from urban dwellings of Lahore, Pakistan: Congener profile, toxicity equivalency, and human health implications. Indoor Air 2021, 31, 1417–1426. [Google Scholar] [CrossRef] [PubMed]
  87. Tue, N.M.; Takahashi, S.; Suzuki, G.; Isobe, T.; Viet, P.H.; Kobara, Y.; Seike, N.; Zhang, G.; Sudaryanto, A.; Tanabe, S. Contamination of indoor dust and air by polychlorinated biphenyls and brominated flame retardants and relevance of non-dietary exposure in Vietnamese informal e-waste recycling sites. Environ. Int. 2013, 51, 160–167. [Google Scholar] [CrossRef]
  88. MacIntosh, D.L.; Minegishi, T.; Fragala, M.A.; Allen, J.G.; Coghlan, K.M.; Stewart, J.H.; McCarthy, J.F. Mitigation of building-related polychlorinated biphenyls in indoor air of a school. Environ. Health 2012, 11, 24. [Google Scholar] [CrossRef] [Green Version]
  89. Harrad, S.; Goosey, E.; Desborough, J.; Abdallah, M.A.-E.; Roosens, L.; Covaci, A. Dust from U.K. Primary School Classrooms and Daycare Centers: The Significance of Dust As a Pathway of Exposure of Young U.K. Children to Brominated Flame Retardants and Polychlorinated Biphenyls. Environ. Sci. Technol. 2010, 44, 4198–4202. [Google Scholar] [CrossRef]
  90. Bannavti, M.K.; Jahnke, J.C.; Marek, R.F.; Just, C.L.; Hornbuckle, K.C. Room-to-Room Variability of Airborne Polychlorinated Biphenyls in Schools and the Application of Air Sampling for Targeted Source Evaluation. Environ. Sci. Technol. 2021, 55, 9460–9468. [Google Scholar] [CrossRef] [PubMed]
  91. Knobeloch, L.; Turyk, M.; Imm, P.; Anderson, H. Polychlorinated biphenyls in vacuum dust and blood of residents in 20 Wisconsin households. Chemosphere 2012, 86, 735–740. [Google Scholar] [CrossRef]
  92. Wang, W.; Huang, M.J.; Zheng, J.S.; Cheung, K.C.; Wong, M.H. Exposure assessment and distribution of polychlorinated biphenyls (PCBs) contained in indoor and outdoor dusts and the impacts of particle size and bioaccessibility. Sci. Total Environ. 2013, 463–464, 1201–1209. [Google Scholar] [CrossRef] [PubMed]
  93. Ward, M.H.; Colt, J.S.; Metayer, C.; Gunier, R.B.; Lubin, J.; Crouse, V.; Nishioka, M.G.; Reynolds, P.; Buffler, P.A. Residential exposure to polychlorinated biphenyls and organochlorine pesticides and risk of childhood leukemia. Environ. Health Perspect 2009, 117, 1007–1013. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  94. Bouchard, M.F.; Oulhote, Y.; Sagiv, S.K.; Saint-Amour, D.; Weuve, J. Polychlorinated biphenyl exposures and cognition in older U.S. adults: NHANES (1999-2002). Environ. Health Perspect 2014, 122, 73–78. [Google Scholar] [CrossRef] [Green Version]
  95. IARC. Iarc Monographs on The Evaluation of Carcinogenic Risks to Humans: Polychlorinated Biphenyls and Polybrominated Biphenyls; IARC, Ed.; International Agency for Research on Cancer: Lyon, France, 2015; Volume 107. [Google Scholar]
  96. Cheng, Z.; Zhang, X.; Bassig, B.; Hauser, R.; Holford, T.R.; Zheng, E.; Shi, D.; Zhu, Y.; Schwartz, S.M.; Chen, C.; et al. Serum polychlorinated biphenyl (PCB) levels and risk of testicular germ cell tumors: A population-based case-control study in Connecticut and Massachusetts. Environ. Pollut. 2021, 273, 116458. [Google Scholar] [CrossRef]
  97. Lim, J.E.; Nam, C.; Yang, J.; Rha, K.H.; Lim, K.M.; Jee, S.H. Serum persistent organic pollutants (POPs) and prostate cancer risk: A case-cohort study. Int. J. Hyg. Environ. Health 2017, 220, 849–856. [Google Scholar] [CrossRef]
  98. Parada, H., Jr.; Sun, X.; Tse, C.K.; Engel, L.S.; Hoh, E.; Olshan, A.F.; Troester, M.A. Plasma levels of polychlorinated biphenyls (PCBs) and breast cancer mortality: The Carolina Breast Cancer Study. Int. J. Hyg. Environ. Health 2020, 227, 113522. [Google Scholar] [CrossRef]
  99. Koual, M.; Cano-Sancho, G.; Bats, A.S.; Tomkiewicz, C.; Kaddouch-Amar, Y.; Douay-Hauser, N.; Ngo, C.; Bonsang, H.; Delomenie, M.; Lecuru, F.; et al. Associations between persistent organic pollutants and risk of breast cancer metastasis. Environ. Int. 2019, 132, 105028. [Google Scholar] [CrossRef]
  100. Obaid, M.F.; Ruiz, P. Polychlorinated biphenyls: New evidence from the last decade. Toxicol. Ind. Health 2016, 32, 1825–1847. [Google Scholar] [CrossRef]
  101. Park, E.Y.; Kim, J.; Park, E.; Oh, J.K.; Kim, B.; Lim, M.K. Serum concentrations of persistent organic pollutants and colorectal cancer risk: A case-cohort study within Korean National Cancer Center Community (KNCCC) cohort. Chemosphere 2021, 271, 129596. [Google Scholar] [CrossRef] [PubMed]
  102. WHO. Cancers. Available online: https://www.who.int/news-room/fact-sheets/detail/cancer (accessed on 9 September 2022).
  103. Arrebola, J.P.; Fernandez, M.F.; Martin-Olmedo, P.; Molina-Molina, J.M.; Sanchez-Perez, M.J.; Sanchez-Cantalejo, E.; Molina-Portillo, E.; Exposito, J.; Bonde, J.P.; Olea, N. Adipose tissue concentrations of persistent organic pollutants and total cancer risk in an adult cohort from Southern Spain: Preliminary data from year 9 of the follow-up. Sci. Total Environ. 2014, 500–501, 243–249. [Google Scholar] [CrossRef] [Green Version]
  104. Charles, D.; Berg, V.; Nost, T.H.; Bergdahl, I.A.; Huber, S.; Ayotte, P.; Wilsgaard, T.; Averina, M.; Sandanger, T.; Rylander, C. Longitudinal changes in concentrations of persistent organic pollutants (1986-2016) and their associations with type 2 diabetes mellitus. Environ. Res. 2021, 204, 112129. [Google Scholar] [CrossRef]
  105. Kim, Y.A.; Park, J.B.; Woo, M.S.; Lee, S.Y.; Kim, H.Y.; Yoo, Y.H. Persistent Organic Pollutant-Mediated Insulin Resistance. Int. J. Environ. Res. Public Health 2019, 16, 448. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  106. Mansouri, E.H.; Reggabi, M. Association between type 2 diabetes and exposure to chlorinated persistent organic pollutants in Algeria: A case-control study. Chemosphere 2021, 264, 128596. [Google Scholar] [CrossRef] [PubMed]
  107. Aminov, Z.; Carpenter, D.O. Serum concentrations of persistent organic pollutants and the metabolic syndrome in Akwesasne Mohawks, a Native American community. Environ. Pollut. 2020, 260, 114004. [Google Scholar] [CrossRef] [PubMed]
  108. Lee, H.A.; Park, S.H.; Hong, Y.S.; Ha, E.H.; Park, H. The Effect of Exposure to Persistent Organic Pollutants on Metabolic Health among KOREAN Children during a 1-Year Follow-Up. Int. J. Environ. Res. Public Health 2016, 13, 270. [Google Scholar] [CrossRef] [Green Version]
  109. Pruvost-Couvreur, M.; Bechaux, C.; Riviere, G.; Le Bizec, B. Impact of sociodemographic profile, generation and bioaccumulation on lifetime dietary and internal exposures to PCBs. Sci. Total Environ. 2021, 800, 149511. [Google Scholar] [CrossRef]
  110. Baba, T.; Ito, S.; Yuasa, M.; Yoshioka, E.; Miyashita, C.; Araki, A.; Sasaki, S.; Kobayashi, S.; Kajiwara, J.; Hori, T.; et al. Association of prenatal exposure to PCDD/Fs and PCBs with maternal and infant thyroid hormones: The Hokkaido Study on Environment and Children’s Health. Sci. Total Environ. 2018, 615, 1239–1246. [Google Scholar] [CrossRef] [Green Version]
  111. Hisada, A.; Shimodaira, K.; Okai, T.; Watanabe, K.; Takemori, H.; Takasuga, T.; Koyama, M.; Watanabe, N.; Suzuki, E.; Shirakawa, M.; et al. Associations between levels of hydroxylated PCBs and PCBs in serum of pregnant women and blood thyroid hormone levels and body size of neonates. Int. J. Hyg. Environ. Health 2014, 217, 546–553. [Google Scholar] [CrossRef]
  112. Boutot, M.E.; Whitcomb, B.W.; Abdelouahab, N.; Baccarelli, A.A.; Boivin, A.; Caku, A.; Gillet, V.; Martinez, G.; Pasquier, J.C.; Zhu, J.; et al. In Utero Exposure to Persistent Organic Pollutants and Childhood Lipid Levels. Metabolites 2021, 11, 657. [Google Scholar] [CrossRef] [PubMed]
  113. Matovu, H.; Li, Z.M.; Henkelmann, B.; Bernhoft, S.; De Angelis, M.; Schramm, K.W.; Sillanpaa, M.; Kato, C.D.; Ssebugere, P. Multiple persistent organic pollutants in mothers’ breastmilk: Implications for infant dietary exposure and maternal thyroid hormone homeostasis in Uganda, East Africa. Sci. Total Environ. 2021, 770, 145262. [Google Scholar] [CrossRef] [PubMed]
  114. Schuhmacher, M.; Mari, M.; Nadal, M.; Domingo, J.L. Concentrations of dioxins and furans in breast milk of women living near a hazardous waste incinerator in Catalonia, Spain. Environ. Int. 2019, 125, 334–341. [Google Scholar] [CrossRef] [PubMed]
  115. Guo, F.; Yin, S.; Wang, H.; Zhang, J.; Liu, Y.; Aamir, M.; Liu, W. Polychlorinated biphenyls (PCBs) in the colostrum samples from the Yangtze River Region: Exposure profile and risk assessment. Environ. Pollut. 2021, 285, 117253. [Google Scholar] [CrossRef] [PubMed]
Ijerph 19 13923 g001 550
Figure 1. Chemical structure of PCBs (m and n denote number of chlorine atoms on each ring).
Figure 1. Chemical structure of PCBs (m and n denote number of chlorine atoms on each ring).
Ijerph 19 13923 g001
Ijerph 19 13923 g002 550
Figure 2. Sources of PCB in the air, human exposure, and possible health impacts.
Figure 2. Sources of PCB in the air, human exposure, and possible health impacts.
Ijerph 19 13923 g002
Table
Table 1. Concentration of PCBs in outdoor environments around the world.
Table 1. Concentration of PCBs in outdoor environments around the world.
SettingLocation Sample/Sampling Area Concentration Dominant Congeners Reference
Ambient AirPatagonia, Argentina Ambient air at 11 sites Σ38PCBs: 25 pg/m3PCB-18, 31, 28,
95, 99, 149, 118, and 138		[51]
Arctic Ocean Snow surface ΣPCB flux: 14.4 pg/cm2 per yearPCB-5, 11, and 52[52]
Fildes Peninsula, West AntarcticaAir samples Σ19PCBs: 1.5–29.7 pg/m3PCB-11[38]
Dalian, ChinaFine particulate matter PCBs in PM2.5: 0.04–0.65 pg/m3PCB-105, 138, 118, 101, 153 and 183[53]
Tainan, TaiwanAmbient air at 1 industrial, 2 urban, and 1 rural areaAverage dry deposition flux of total PCBs: 0.540–1.94 pg WHO-TEQ/m2 per day-[54]
Hangzhou and Yangtze River Delta, ChinaAgricultural area (A.A.) and eco-industrial park (EIP)Σ29 PCBs:
  • AA: PCB-189, 170, and -28 in winter and summer
  • EIP: PCB-189, 170 and -28 in winter; PCB-28 in summer
[55]
  • AA: 224–482 pg/m3 (winter); 135–553 pg/m3 (summer)
  • EIP: 233–537 pg/m3 (winter) 39.9–254 pg/m3(summer)
Valencia Region, SpainAmbient air at 7 monitoring stations
  • Σdl-PCB:1.18 to 10.00 fg TEQ/m3
  • Industrial area: 2.20 fg TEQ/m3
  • Urban areas: 3.11 fg TEQ/m3
-[56]
Urban AreasMadrid, Spain68 ambient air samples Total PCBs: 437 pg/m3PCB-28, 52, 101, 138, 153, and 180 [22]
Turkey32 urban and rural sites Annual average Σ43PCBs: 108 ±132 pg/m3.
  • Rural: PCB-104,114, 118, 123, 151, 167, and 203
  • Urban: PCB-101, 138, 153 and 118
[57]
  • Highest mean at urban sites: 403 ± 428 pg/m3
  • Highest mean at rural sites: 217 ± 353 pg/m3
Naples, ItalyAtmospheric bulk deposition Deposition flux of Σ18PCBs: 0.075–1.22 ng/m2/dayPCB-28, 138, 153 and 180[44]
Industrial AreasKocaeli, Turkey Ambient air at 23 sites Σ41PCB: 4152 ± 6072 pg/m3PCB-18, 28, 31 and 33 [42]
Eastern ChinaAmbient air around municipal solid waste incineratorΣ18PCBs:
81 ± 46 pg/m3 (summer); 70 ± 13 pg m3 (winter)		PCB-28, 52, 101, and 138[20]
North Rhine-Westphalia, GermanyAmbient air at silicone rubber production siteΣ6PCB: 300–1500 pg/m3PCB 47, 51 and 68[41]
Dilovasi region, TurkeyAmbient air at 23 industrial sites Σ41PCB: 4152 ± 6072 pg/m3 PCB-28, 18, 31, and 33[58]
Pohang, South KoreaBulk deposition at steel manufacturing plant Σ12PCB deposition fluxes: 1.3–4.7 ng/m2/dayPCB- 77, 118, and 105[59]
Aliaga region, TurkeyAmbient air at 40 industrial sites Σ35PCB: 349–94,363 pg/m3PCB-18, 28, 31, 33, 52, and 49[60]
E-waste Recycling SitesTaizhou, China17 ambient air samples Σ57PCB: 37.75–65.83 ng/m3-[61]
Chennai, India Ambient air 3.6–53 ng/gtetra (4-CB), penta (5-CB) and hexa (6-CB) homologs[62]
ChinaAmbient air7825–76,330 pg/m3-[28]
Table
Table 2. Concentration of PCBs in indoor environments in different settings.
Table 2. Concentration of PCBs in indoor environments in different settings.
SettingsLocation Sample/Sampling Area Concentration Dominant Congeners Reference
WorkplaceHong Kong, ChinaAir-conditioner filter dustΣ37PCBs: 46.8–249 ng/gPCB-77, 194, and 199 [76]
Abraka and Warri, NigeriaIndoor dust at electronic repair workshopΣ28 PCB: 96.6–3949 ng/gHexa-PCB[77]
Durban, South AfricaDust Σ3PCBs: 235 ng/g-[78]
North-Rhine Westphalia, GermanyAir Σ28PCB: 92–2797 ng/m3PCB-28, 52 and 101[75]
FranceAirΣ19PCB: 1.75 ± 1.82 ng/m3-[79]
ResidentVietnamSettled dust Σ209 PCB: 11–1900 ng/g-[80]
CanadaAirΣ7PCB: 455 pg/m3 -[64]
Czech RepublicAir and dustΣ7PCB: 467 pg/m3 (air); 75.1 ng/g (dust)-[64]
Kopawa, NepalDustƩ30PCBs: 9.64–16.5 ng/gTetra-PCBs followed by penta, hexa, and hepta-CBs[81]
Brno,
Czech Republic		AirΣ7PCB: 89 pg/m3 (summer); 61 pg/m3 (winter)Tri-tetra, and hepta-hexa PCBs[82]
Belgium, Italy, Spain, and PortugalAirΣ7PCBs: 306 pg/m3PCB-28, 52 and 101[83]
Farum, DenmarkAirƩ24PCBs: 168–3843 ng m3PCB-28 and 52[84]
Bursa, TurkeyAir Σ40PCBs Penta-, tetra- and tri-CBs[63]
  • Living rooms: 604 ± 210 pg/m3 (summer); 362 ± 167 pg/m3 (autumn)
  • Kitchens: 639 ± 2514 pg/m3 (summer); 309 ± 93 pg/m3 (autumn)
Brondby Strand Parkerne, DenmarkAir, vacuum cleaner dust, and surface wipesΣ15PCB: 2330 ng/m3 (air); 12.000 ng/g (dust); 529 ng/wipe (surface wipes) Tri- and Tetra PCBs[69]
Thessaloniki, GreeceDustΣ15PCBs: 3.04–9.68 ng/gPCB-52, 28 + 31 and 101[85]
Lahore, Pakistan Dust∑35 PCB: 0.27–152.9 ng/g Tri- and Tetra PCBs[86]
Hai Phong city and Hung Yen province, VietnamAir and DustPCBs level in dust: 3.6–320 ng/g
PCBs level in air: 1000–1800 pg/m3		In dust: penta- and hexaCBs
In air: triCBs 		[87]
SchoolUnited StatesAir100–276 ng/m3-[88]
United StatesAir0.5–194 ng/m3 [49]
West Midlands, U.K.DustΣ8PCBs: 1.2–560 ng/g [89]
Indiana and Iowa, United States 0.5–194 ng/m3-[49]
Iowa, United States Air 1.54–35.75 ng/m3-[90]
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Othman, N.; Ismail, Z.; Selamat, M.I.; Sheikh Abdul Kadir, S.H.; Shibraumalisi, N.A. A Review of Polychlorinated Biphenyls (PCBs) Pollution in the Air: Where and How Much Are We Exposed to? Int. J. Environ. Res. Public Health 2022, 19, 13923. https://doi.org/10.3390/ijerph192113923

AMA Style

Othman N, Ismail Z, Selamat MI, Sheikh Abdul Kadir SH, Shibraumalisi NA. A Review of Polychlorinated Biphenyls (PCBs) Pollution in the Air: Where and How Much Are We Exposed to? International Journal of Environmental Research and Public Health. 2022; 19(21):13923. https://doi.org/10.3390/ijerph192113923

Chicago/Turabian Style

Othman, Naffisah, Zaliha Ismail, Mohamad Ikhsan Selamat, Siti Hamimah Sheikh Abdul Kadir, and Nur Amirah Shibraumalisi. 2022. "A Review of Polychlorinated Biphenyls (PCBs) Pollution in the Air: Where and How Much Are We Exposed to?" International Journal of Environmental Research and Public Health 19, no. 21: 13923. https://doi.org/10.3390/ijerph192113923

APA Style

Othman, N., Ismail, Z., Selamat, M. I., Sheikh Abdul Kadir, S. H., & Shibraumalisi, N. A. (2022). A Review of Polychlorinated Biphenyls (PCBs) Pollution in the Air: Where and How Much Are We Exposed to? International Journal of Environmental Research and Public Health, 19(21), 13923. https://doi.org/10.3390/ijerph192113923

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