Persistent organic pollutants on human and sheep hair and comparison with POPs in indoor and outdoor air
1Environment Protection Agency, Freetown, Sierra Leone.
2Environment and Life Sciences Research Center, Kuwait Institute for Scientific Research, P.O. Box 24885, Safat 13109, Kuwait.
Correspondence to: Dr. Bondi Gevao, Executive Chairman, Environment Protection Agency, 92 Dundas Street, Freetown, Sierra Leone. E-mail:
This study compared the concentration of persistent organic pollutants (POPs) in air derived from polyurethane-based passive samplers to those of hair samples collected from humans and sheep. Human scalp hair samples were obtained from 24 healthy individuals and ten sheep (Ovis aries) during indoor and outdoor polyurethane foam plug ambient sampling. The samples were analyzed for polycyclic aromatic hydrocarbons (PAHs) and polybrominated diphenyl ethers (PBDEs). ∑PBDE concentrations ranged 0.6-50 ng·g-1 (mean, 18.6 ± 13 ng·g-1) for humans and 0.6-1.4 ng·g-1 (mean, 1.1 ± 0.25 ng·g-1) for sheep. The ∑PAH concentrations were log-normally distributed in human hair ranging 98-2529 ng·g-1 (mean, 460 ± 538 ng·g-1), whereas concentrations for sheep hair samples ranged 168-526 ng·g-1 (mean, 334 ± 117 ng·g-1). Strong correlations (P-values < 0.01) were found between concentrations of PAHs and PBDEs in human and sheep hair with concentrations measured in indoor and outdoor air, respectively. Evidence generated from this preliminary study suggests that hair might be used for the environmental monitoring of POPs in remote sites to provide a first-order estimate of ambient levels. Further studies are required to understand the uptake profiles and validate the use of hair as a sampling medium for POPs in ambient air.
Persistent organic compounds such as polycyclic aromatic hydrocarbons (PAHs) and polybrominated diphenyl ethers (PBDEs) have the propensity to enter the gas phase at ambient temperatures and undergo long-range atmospheric transport. These chemicals have received intense international attention because of their ubiquity, bioaccumulation potential, and detrimental biological effects[1-3]. The combination of their resistance to metabolism and lipophilicity means that they will bioaccumulate and be transported through food chains. In addition, they are subject to long-range transport and have been detected in remote areas where they have never been used[4,5]. Since atmospheric transport is the principal vehicle for the movement and global distribution of these chemicals, significant efforts are being made on identifying their ambient sources[6-9], transport pathways[4,10,11], and fate[12-14]. Until recently, there was a paucity of reliable environmental data on the levels of most POP chemicals in the Middle East, most of Africa, and Asia, from which to assess the effectiveness of international efforts to minimize the release of these chemicals to the environment. This is partly due to the lack of appropriate analytical facilities and trained personnel in developing countries. High-volume air sampling procedures, for example, are expensive, often require skilled personnel for sampling, and require electricity for their operation. Recently, passive samplers such as semipermeable membrane devices[15,16], polyurethane foam (PUF)[17-19], polymer-coated glass[20,21], XAD filled tubes, and tristearin-coated fiberglass sheets have been developed and validated for measuring POPs in the atmosphere.
It is desirable to have alternative sampling technologies that will provide identical information at lower costs. In the past, vegetation such as grass, pine needles[24-26], mosses[27,28], and lichens were studied to make inferences about POP concentrations in the air. The main advantage of passive sampling is that it is cheap and does not require skilled personnel for its deployment, which makes widespread deployment possible especially in remote locations. The simplistic design and operation have made passive samplers attractive for developing countries that are still developing their capabilities of POPs sampling and analyses. Some studies have used hair as a potential matrix for estimating semi-volatile organic pollutants in air[30,31] and for POP assessment[32-35]. Since hair has a high lipid content, it can be a suitable medium for the retention of POPs. Hair has similar attributes with other passive samplers, including the simplicity of sample collection, storage, and transportation[31,36-38]. Sample handling protocols are least stringent for hair, and, as such, sampling does not require very skilled personnel. Since hair sampling is non-invasive, subject compliance is high as it is socially and ethically acceptable compared to other samplers. Samples can be easily obtained from people of different age groups and sex. As such, broader geographical coverage can be achieved with little effort[31,36-38], making large-scale mapping exercises and reconnaissance surveys very feasible and cost-effective.
Some studies have tried to investigate the link between concentrations of POPs in hair and internal tissues in humans and animals to determine whether hair concentrations reflect body burdens[31,36-41]. Tirler et al. (2001) suggested that hair could be used as a passive sampler for POPs when determining the indoor air levels of lindane in rural Germany. The most direct evidence, so far, to assess the potential of hair as a passive sampler of POPs comes from the work of Schramm. In laboratory microcosm experiments, hair was fumigated with gaseous PCBs and PCDD/Fs, and the kinetics of uptake were evaluated. Rapid uptake was observed, with equilibrium established within hours of exposure. The current study investigated the comparability of POP concentration in air derived from polyurethane-based passive sampling and hair to assess if hair can be used for the environmental monitoring of POPs. The approach we adopted was to passively sample the air in homes of volunteers that consented to provide hair samples, using PUF passive samplers deployed over a six-week period. In addition, hair was sampled from ten randomly selected sheep during the same period as the outdoor deployment of passive samplers. Indoor air and ambient (outdoor) air concentrations have been published previously[17,43]. Here, we report the concentrations of PAHs and PBDEs in hair and examine the relationships between hair concentrations in air and passive samplers.
Sample collection and pretreatment
Twenty-four healthy males in a broad age group were selected for the collection of scalp hair samples in Kuwait. Passive samplers were deployed in their homes. Using stainless steel scissors, sheep (Ovis aries) hair samples were collected across Kuwait from 10 randomly selected sheep. The hair samples were stored at
The PUF disks used to collect chemicals from the air were certified as flame retardant free and purchased from Tisch Environmental (OH, USA). The PUF disks were cleaned for 48 h using dichloromethane in a giant Soxhlet. The pre-extracted PUF plugs were dried in a clean desiccator under vacuum and stored in solvent rinsed amber glass jars lined with solvent rinsed aluminum foil to avoid contamination during storage. In the field, the PUF was suspended in the center of two stainless steel dishes between washers by using solvent-rinsed tweezers. The samplers were attached to a pole at the site of deployment. Outdoor deployment was on roof-tops where the air could be considered well mixed. Samples were deployed at 17 sites over a six-week period.
Chemicals and reagents
Analytical grade solvents were procured from VWR Scientific (NY, USA). The silica (100-200 mesh), alumina, and sodium sulfate used were manufactured by Baker (NJ, USA). The deuterated PAH cocktail standard ES-2044 was used as the internal standard. This standard contains pyrene-d10, phenanthrene-d10, fluoranthene-d10, benzo[a]pyrene-d12, and benzo[ghi]perylene-d12. The other analytical standard used was EO-5103 for PBDEs, with a congener mix of the following: 17, 28, 47, 66, 71, 85, 99, 100, 138, 153, 154, 183, 190, and 209. Additionally, brominated diphenyl ether (BDE) 35 (EO-4109) and BDE 181 (EO-4927) were purchased from Cambridge Isotope Laboratories (CIL, Andover MA, USA) were added at a concentration of 100 ng.
Extraction and analyses
PUF disk samples were extracted in a Soxhlet apparatus using a 1:1 v/v mixture of acetone:hexane. Prior to extraction, the samples were spiked with a range of surrogates to monitor analytical recovery. The extracts were cleaned by column chromatography using 10 g of silica and 5 g of alumina column. They were further cleaned by gel permeation chromatography using 6 g of Biobeads SX 3 (BioRad, Hertfordshire, UK). The final volume was made up with 500 μL of isooctane and spiked with internal standards.
For the extraction of hair samples, 0.2-0.5 g of finely ground hair were weighed in a 40 mL vial; spiked with a range of ES-2044, EO-5103, EO-4109, and EO-4927; and incubated overnight at 40 °C in 4 mL of a 3 N HCl and 3 mL of hexane:dichloromethane (4:1, v/v) to monitor analytical recovery. The analytes of interest were extracted from the incubation medium by liquid-liquid extraction with 2 × 4 mL hexane:dichloromethane (4:1, v/v). The organic extracts were combined and dried on a bed of anhydrous Na2SO4 to remove any residual water. Column chromatography was used for removing the interfering compounds, using 2 g of silica and 1 g of alumina (and 0.5 cm anhydrous Na2SO4 at the top of the column to prevent the column from coming into contact with air) and eluting the compounds of interest with
The PAHs in the sample extracts were analyzed using splitless injection (injection volume, 1 μL) on a 30 m HP-5ms column (0.25 mm i.d., 0.25 μm film thickness) on a Shimadzu GC-17A (Shimadzu, Tokyo, Japan) gas chromatograph using helium as a carrier gas. The method is described in detail elsewhere. An internal standard method for identification and quantification against five calibration standards was used that contained fifteen PAHs (acenaphthylene, acenaphthene, anthracene, benz[a]anthracene,
Consequent to the PAH analyses, the sample volume was reduced to 50 μL in dodecane for PBDE analysis. PBDEs were analyzed using splitless injection on a 30 m HP-5ms column (0.25 mm i.d., 0.25 µm film thickness) with an Agilent 6890N gas chromatograph using helium as carrier gas. Details of the method are given elsewhere. Identification and quantification were carried out against five calibration standards. BDE 209 was analyzed on a 15 m DB-5ms column (0.25 mm i.d., 0.25 μm film thickness). The GC oven conditions, identification, and quantitation followed those of Gevao et al..
Peaks were positively identified if they were within ± 0.05 min of the retention time in the calibration standard. They were quantified only if the response exceeded three times the background noise, and the isotopic ratio between the quantitative and the confirmation ions was within ± 20% of the theoretical value. The concentration of fortified hair samples was extrapolated to a signal-to-noise level of 3 for calculating the detection limit. The detection limits for PBDEs ranged 5-60 pg·g-1 with the exception to BDE 209 for which the detection limit was 1.5 ng·g-1. The detection limits for PAHs ranged 1.0 ≠ 12.8 pg·g-1. Laboratory blanks, comprised of incubation solution and treated as samples, were processed for every five samples. The concentration in blanks was subtracted from those in the sample extracts. Average recoveries [(%) ± standard deviation (SD)] for surrogates spiked in samples were between 85% ± 10% for BDE 35, 74% ± 5% for BDE 181, whereas those of PAHs varied from 65% ± 8% to 95% ± 5%.
RESULTS AND DISCUSSION
The estimated air concentrations were derived assuming a sampling rate of 3.0 m3 air per day[47,48] derived from calibration studies against an active sampler. Applying this sampling rate, the PUF disks would have sampled 105 m3 of air over the six-week deployment period. The sampling rate has been shown to be linear for compounds with KOA larger than 108.5 for the first 100 days.
PBDEs in hair
The following congeners were detected: BDEs 28, 47, 99, 100, 153, 154, 183, and 209. Their sum is referred to as ∑PBDEs. None of the sheep samples contained BDEs 183 or 209 above detection limits. ∑PBDE concentrations measured in human and sheep hair samples are summarized in Figures 1 and 2, respectively, and detailed congener-specific measured concentrations are provided in Tables 1 and 2, respectively. Concentrations ranged 0.6-50 ng·g-1 of human hair with a mean of 18.6 ± 13 ng·g-1. For ∑PBDEs, in human hair, BDE 209, constituted ~87%, followed by BDE 47 (7.3%), BDE 99 (7.1%), and BDE 28 (2.8%) with the remaining congeners (BDEs 100, 153, and 154) together contributing approximately 3.5%. In sheep hair samples, the concentrations of ∑PBDEs ranged 0.609-1.410 ng·g-1 with a mean of 1.100 ± 0.250 ng·g-1.
PBDE concentrations (ng·g-1) in human hair
|H 10||0.04||1.11||0.12||0.15||0.04||0.03||< d.l.||13.02||14.52|
|H 16||0.03||0.67||0.14||0.11||0.04||0.11||< d.l.||< d.l.||1.10|
|H 17||0.07||0.36||0.06||0.08||0.00||0.03||0.02||< d.l.||0.63|
PBDEs in animals (pg·g-1)
|AH 1||77.3||631.5||55.8||255.5||14.5||12.4||< d.l.||< d.l.||1047.0|
|AH 2||38.8||350.8||47.8||264.7||24.8||19.2||< d.l.||< d.l.||746.1|
|AH 3||89.7||801.6||78.0||362.2||35.9||42.4||< d.l.||< d.l.||1409.8|
|AH 4||61.5||475.3||59.5||297.8||36.9||21.6||< d.l.||< d.l.||952.6|
|AH 5||73.7||666.0||76.4||298.7||17.9||23.5||< d.l.||< d.l.||1156.3|
|AH 6||64.4||542.0||50.8||290.1||22.9||45.9||< d.l.||< d.l.||1016.2|
|AH 7||69.7||786.8||93.6||409.6||14.9||18.5||< d.l.||< d.l.||1393.1|
|AH 8||73.0||659.3||66.8||331.6||25.5||32.6||< d.l.||< d.l.||1188.9|
|AH 9||62.6||640.5||66.4||295.4||26.0||12.4||< d.l.||< d.l.||1103.3|
|AH 10||27.5||237.0||201.4||115.7||27.0||< d.l.||< d.l.||< d.l.||608.6|
|Mean||63.8||579.1||79.7||292.1||24.6||25.4||< d.l.||< d.l.||1062.2|
The concentrations in human hair very closely track indoor air concentrations [Figure 3A], and the two are remarkably correlated (P-value = 0.004). Similarly, a significant correlation (P-value < 0.001) is observed between sheep hair and outdoor air concentrations of PBDEs estimated from passive sampling measurements across Kuwait [Figure 3B]. Other studies have reported PBDEs in animal hair; for example, D’Havé et al. studied the concentrations in hair and other body tissues in 32 European hedgehogs
PBDE congener profiles
As mentioned above, the congener distribution of human hair is dominated by BDE 209, which constitutes ca. 87% of the ∑PBDEs measured in human hair. This congener is, however, absent in sheep hair samples. In a previous study, high levels of BDE 209 were found in house dust in Kuwait. The dominance of BDE 209 in dust and human hair samples suggests that deca-technical mixture is a dominant contributor of PBDEs to indoor air in Kuwait. If we exclude BDE 209 and express the congener contribution as the percentage of BDEs 28, 47, 100, 99, 85, 153, 154, and 183, it shows that the penta-congener mixture is an important technical mixture in Kuwait. The congener distributions in hair, indoor air, and outdoor air, excluding BDE 209, as well as of Bromkal 70-5DE, a commercially marketed mixture for comparison, are given in Figure 4. There are a few observations of importance in this profile. First, the composition in human hair very closely matches the technical penta-mixture, suggesting volatilization from penta-treated products is a significant indoor source. Second, the proportion of BDE 47, the dominant congener in the technical mixture in sheep and ambient air, is a reflection of the differences in the volatility of the congeners relative to each other. This hypothesis comes from the work by Bruckman et al., who reported a five-fold increase in PBDE levels in a room after the TV was left on for several hours. In another study, volatilization of BFRs from television, computers, and printers was reported. The authors concluded that annual BFRs emissions from TV and monitors were about 0.1% and 0.4%, respectively.
PAHs concentrations in hair
The concentration of PAHs in human hair is summarized in Figure 5, and detailed compound-specific information is given in Figure 6A and Table 3. The concentration of ∑PAHs varied from 98 to 2529 ng·g-1 of hair with a mean concentration of 460 ± 538 ng·g-1, dominated by low molecular weight tricyclic PAHs contributing 75%. Phenanthrene was the most abundant compound contributing ca. 42%, followed by fluorene (12%), anthracene-fluoranthene (10%), and pyrene (7%). In the only other study of PAHs in human hair, Toriba et al. reported a mean ∑PAH concentration of 176 ng·g-1, which is lower than those one in this study by a factor of ~3. The compound distribution in their study is similar to that reported here, with the major compounds in decreasing order of importance being phenanthrene (60%), fluoranthene (14%), pyrene (10%), and fluorene-anthracene (5%). The high molecular weight PAHs were below the detection limits, as is the case in this study.
Figure 6. ∑PAH concentration in human hair and indoor air. (B) ∑PAH concentration in animal hair and outdoor air. PAH: Polycyclic aromatic hydrocarbon.
PAHs in human hair (ng·g-1)
|H 1||40.3||265.6||217.9||537.7||20.4||72.8||74.8||3.7||10.5||< d.l.||< d.l.||1244|
|H 2||15.3||66.9||76.8||219.6||7.6||29.4||36.0||1.2||4.0||< d.l.||< d.l.||457|
|H 3||8.1||41.4||39.1||142.4||5.7||30.0||29.7||2.6||6.6||< d.l.||< d.l.||306|
|H 4||2.1||36.9||35.0||130.7||12.7||20.5||33.8||1.9||7.3||< d.l.||< d.l.||281|
|H 6||57.2||17.0||14.7||74.0||5.2||21.9||29.5||3.3||9.9||< d.l.||< d.l.||233|
|H 7||6.6||48.7||40.0||103.4||3.7||13.7||17.4||0.7||2.7||< d.l.||< d.l.||237|
|H 9||0.9||13.9||17.0||95.8||7.1||32.2||28.0||2.3||7.0||< d.l.||< d.l.||204|
|H 10||2.3||20.5||25.2||71.1||4.3||10.1||18.4||1.5||3.5||< d.l.||< d.l.||157|
|H 11||64.2||34.2||39.4||138.2||10.5||24.3||39.7||3.2||6.7||51.9||< d.l.||412|
|H 12||31.1||9.0||9.5||44.0||2.5||9.1||14.3||4.6||3.9||< d.l.||< d.l.||128|
|H 13||3.0||15.0||47.1||238.2||24.8||15.4||18.6||1.0||2.1||< d.l.||< d.l.||365|
|H 15||14.9||32.6||124.3||552||125.4||153.3||99.5||4.7||8.0||< d.l.||< d.l.||1114|
|H 16||2.4||10.3||14.4||54.2||4.2||9.6||12.9||1.7||3.3||< d.l.||< d.l.||113|
|H 17||25.5||35.8||443.0||537.6||852.6||537.7||232.0||2.2||6.3||< d.l.||< d.l.||2529|
|H 18||0.3||1.8||21.0||161.4||16.8||7.8||7.9||0.3||0.9||< d.l.||< d.l.||218|
|H 19||0.2||4.1||22.7||392.8||56.0||42.9||22.5||< d.l.||1.4||< d.l.||< d.l.||543|
|H 20||6.3||40.7||45.4||130.6||6.0||18.1||18.7||1.2||2.8||< d.l.||< d.l.||270|
|H 21||0.9||15.5||15.6||45.1||1.5||7.7||8.0||0.7||3.0||< d.l.||< d.l.||98|
|H 22||1.6||27.2||25.3||69.6||2.8||9.0||9.5||0.9||1.5||< d.l.||< d.l.||147|
|H 23||5.9||42.3||38.7||104.6||4.0||13.8||11.4||0.8||2.1||< d.l.||< d.l.||224|
|H 24||2.7||22.3||26.8||81.7||4.1||16.4||16.2||1.5||4.4||< d.l.||< d.l.||176|
Average ∑PAH concentrations in indoor air, concurrently measured using PUF samplers at the time of hair sampling, varied between 1.3 and 16 ng·m-3. The compositional profile of ∑PAHs in human hair measured in this study matches closely that of the indoor air profile (P-value < 0.001) [Figure 6A]. Concurrently measured air concentrations obtained by deploying PUF samplers across Kuwait ranged between 5 and 13 ng·m-3 during the same period sheep hair samples were obtained. The average concentrations of individual compounds in sheep hair closely track ambient air concentrations [Figure 6B] and are significantly correlated (P-value < 0.001).
In sheep hair samples, ∑PAH concentrations varied from 168 to 526 ng·g-1 [Figure 7] with a mean concentration of 334 ± 117 ng·g-1. Detailed compound-specific information is given in Figure 6B and Table 4. The contributions of tricyclic PAHs and tetracyclic PAH were 74% and ca. 22% of the ∑PAHs. The major compounds in order of importance were phenanthrene (44%), fluorene (16%), anthracene (11%), fluoranthene (10%), and pyrene (9%).
PAH concentrations (ng·g-1) in animal hair
|AH 1||AH 2||AH 3||AH 4||AH 5||AH 6||AH 7||AH 8||AH 9||AH 10|
|BbF||12.6||5.7||17.0||< d.l.||< d.l.||< d.l.||< d.l.||< d.l.||< d.l.||9.5|
|BkF||< d.l.||< d.l.||< d.l.||< d.l.||< d.l.||< d.l.||< d.l.||< d.l.||< d.l.||< d.l.|
Hair vs. passive air samplers
The vast majority of studies on pollutants in hair have focused on investigating the relationship between concentrations of pollutants in hair and other body tissues with the view to determine if hair can be used to estimate the contaminant body burden of humans and animals. These studies have presented consistent evidence in support of this hypothesis. Jaspers et al., for example, reported significant correlations between feathers of Buteo buteo, a predatory bird, and other body tissues for some PBDE congeners, but low ones for DDT and others. They suggested this mixed result was due to differences in metabolic rates or differences in external contamination of the feathers. D’Havé et al., also studying POPs in mammals, reported correlations between hair and body tissues (liver, kidney, and muscle) with coefficients varying between 0.72 and 0.78. A lack of any correlation in the case of BDE 99 was also attributed to differences in accumulation rates between different tissues and hair. Gill et al. reported relatively higher concentrations of PCB 52 and 101 in hair compared with those in adipose tissues or serum. The authors contended that this was due to contamination of hair from exogenous sources and/or possible differences in elimination kinetics between congeners. Altshul et al. reported a significant correlation (r = 0.8) between hair and the serum of 10 individuals for p,p'-DDE but non-significant correlations for PCBs and p,p′-DDT. Covaci and Schepens reported similar profiles of PCBs in human hair, serum, milk, and adipose tissue. When concentrations were normalized to lipid, similar concentrations were found among all the matrices for lindane, PCBs, p,p′-DDT, and p,p′-DDE. Nakao et al. reported similar ratios of PCDD/Fs in the blood and hair of six donors, although the actual concentrations were reportedly higher in blood.
The link between indoor pollution and the concentration of pollutants in hair has received far less attention. Neuber and Merkel investigated the relationship between indoor air concentrations of lindane and DDT from wood preservatives and the concentrations of hair in preschool children in rural Germany. Lindane was detected in the vast majority of samples, whereas DDT was present in 30% of the samples, which led them to suggest that hair may be used for assessment of indoor air pollution by lindane and DDT.
One of the main challenges in the interpretation of hair data is distinguishing between endogenous and exogenous sources of contamination[36,38,40,57]. It has been argued that the current hair washing procedures designed to remove “external contamination” from hair cannot distinguish between the two[37,38]. The question that needs to be answered is whether semi-volatile organic compounds in the hair are primarily exogenous or endogenous in origin. The approach to addressing this issue has been to wash hair using different approaches as no standardized procedure has been agreed upon. Hair washing procedures to distinguish exogenous and endogenous fractions of hair have included washing with hot water[31,36,37,39] or washing with water followed by hair shampoo[38,55,58]. Altshul et al. reported a 25%-35% extraction of POPs following a shampoo wash, whereas Nakao et al. found that 50% of PCDD and 65% of PCDFs were removed from hair using the same procedure. At the other extreme, Ostrea et al. noted that no significant differences were observed between paired hair samples, before and after washing, for propoxur to varying percentage removal for other pesticides. It is almost impossible to distinguish between the two using the current methods, and any distinction on the basis of washing is merely operational. Hair has been used extensively in forensic analyses, especially in the field of poisoning and in the diagnosis of certain diseases and nutritional assessments of humans[60-62]. However, there are many studies on trace metals in hair where levels were not consistent with the nutritional status and clinical symptoms of the individuals and did not match other biological indicators (e.g., whole blood, serum, and urine), further putting into question the notion that hair may be reflective of body burden.
Most hydrocarbons, including POPs, are subject to metabolic transformation, which converts them to more polar moieties that can be easily excreted. It has been suggested that, since the hair root is vascularized during growth, pollutants in blood (which are yet to be metabolized) may enter the roots and be stored. However, it is not known what fraction of the body burden actually escapes as intact compounds and becomes stored in hair and other body tissues. In this study, very significant correlations were found between concentrations of both PBDEs and PAHs in hair and ambient air. Since humans spend in excess of 90% of their time indoors, especially in hot arid countries such as Kuwait, the concentrations in human hair were correlated with concentrations of these chemicals in indoor air measured using polyurethane foam passive air samples. Pearson correlation coefficients were very significant for PBDEs (P-value < 0.004) and PAHs (P-value < 0.001). In the case of sheep, the concentrations found in hair were correlated with outdoor concentrations measured using the sample PUF air samplers. The correlations were even better, with
Authors acknowledge the support of Kuwait Institute of Scientific Research for funding this research. Authors are thankful to Mr. Jamal Zafar and Mr. Khaled Al-Matrouk for their assistance in chemical analyses.Authors’ contributions
Made substantial contributions to conception and design of the study and performed data analysis and interpretation: Gevao B, Uddin S
Performed data acquisition, as well as provided administrative, technical, and material support: Al-Bahloul M, Al-Mutairi AAvailability of data and materials
The data is available in the report and as an additional Report at Kuwait Institute for Scientific Research. Additional data and information can be made available at request from individuals interested.Financial support and sponsorship
The study was supported by Kuwait Institute for Scientific Research. The funding body has no role in design and execution of this study.Conflicts of interest
All authors declared that there are no conflicts of interest.Ethical approval and consent to participate
Consent was taken from participants.Consent for publication
© The Author(s) 2022.
1. UNECE. Protocol on persistent organic pollutants under the 1979 convention on long-range transport air pollution. Available from: https://unece.org/sites/default/files/2021-10/1998.POPs_.e.pdf [Last accessed on 19 Jan 2022].
2. UNECE. Preparation of an internationally binding instrument for implementing international action on certain persistent organic pollutants. Available from: http://chm.pops.int/Portals/0/docs/from_old_website/documents/meetings/ceg2/en/ceg2inf2e.html [Last accessed on 19 Jan 2022].
3. Vallack HW, Bakker DJ, Brandt I, et al. Controlling persistent organic pollutants–what next? Environ Toxicol Pharmacol 1998;6:143-75.
4. Beyer A, Mackay D, Matthies M, Wania F, Webster E. Assessing long-range transport potential of persistent organic pollutants. Environ Sci Technol 2000;34:699-703.
5. Ockenden WA, Jones KC. Global fractionation of persistent organic pollutants. Progress in Environmental Science 1999;1:119-51.
6. Breivik K, Alcock R, Li YF, Bailey RE, Fiedler H, Pacyna JM. Primary sources of selected POPs: regional and global scale emission inventories. Environ Pollut 2004;128:3-16.
7. Kemmlein S, Hahn O, Jann O. Emissions of organophosphate and brominated flame retardants from selected consumer products and building materials. Atmos Environ 2003;37:5485-93.
8. Lohmann R, Northcott GL, Jones KC. Assessing the contribution of diffuse domestic burning as a source of PCDD/Fs, PCBs, and PAHs to the U.K. Atmosphere. Environ Sci Technol 2000;34:2892-9.
9. Wilford BH, Harner T, Zhu J, Shoeib M, Jones KC. Passive sampling survey of polybrominated diphenyl ether flame retardants in indoor and outdoor air in Ottawa, Canada: implications for sources and exposure. Environ Sci Technol 2004;38:5312-8.
10. Mackay D, Wania F. Transport of contaminants to the arctic: partitioning, processes and models. Sci Total Environ 1995;160-161:25-38. DOI: 10.1016/0048.
11. Schure AF, Larsson P, Agrell C, Boon JP. Atmospheric transport of polybrominated diphenyl ethers and polychlorinated biphenyls to the Baltic Sea. Environ Sci Technol 2004;38:1282-7.
12. Chen JC, Wong YS, Wang TSM, Hong H, Xu L, Zhang L. Environmental fate and chemistry of organic pollutants in the sediment of Xiamen and Victoria Harbours. Mar Pollut Bull 1995;31:229-36.
13. Iwata H, Tanabe S, Sakai N, Tatsukawa R. Distribution of persistent organochlorines in the oceanic air and surface seawater and the role of ocean on their global transport and fate. Environ Sci Technol 1993;27:1080-98.
14. Saliot A, Bigot M, Bouloubassi I, Lipiatou E, Qiu Y, Scribe P. Transport and fate of hydrocarbons in rivers and their estuaries. Partitioning between dissolved and particulate phases: case studies of the Rhône, France, and the Huanghe and the Changjiang, China. Sci Total Environ 1990;97-98:55-68.
15. Lohmann R, Corrigan BP, Howsam M, Jones KC, Ockenden WA. Further developments in the use of semipermeable membrane devices (SPMDs) as passive air samplers for persistent organic pollutants: field application in a spatial survey of PCDD/Fs and PAHs. Environ Sci Technol 2001;35:2576-82.
16. Ockenden WA, Sweetman AJ, Prest HF, Steinnes E, Jones KC. Toward an understanding of the global atmospheric distribution of persistent organic pollutants: the use of semipermeable membrane devices as time-integrated passive samplers. Environ Sci Technol 1998;32:2795-803.
17. Gevao B, Al-Omair A, Sweetman A, et al. Passive sampler-derived air concentrations for polybrominated diphenyl ethers and polycyclic aromatic hydrocarbons in Kuwait. Environ Toxicol Chem 2006;25:1496-502.
18. Harner T, Ikonomou M, Shoeib M, Stern G, Diamond M. Passive air sampling results for polybrominated diphenyl ethers along an urban-rural transect. Organohalogen Compounds 2002;57:33-6.
19. Jaward FM, Farrar NJ, Harner T, Sweetman AJ, Jones KC. Passive air sampling of polycyclic aromatic hydrocarbons and polychlorinated naphthalenes across Europe. Environ Toxicol Chem 2004;23:1355-64.
20. Farrar NJ, Harner T, Shoeib M, Sweetman A, Jones KC. Field deployment of thin film passive air samplers for persistent organic pollutants: a study in the urban atmospheric boundary layer. Environ Sci Technol 2005;39:42-8.
21. Harner T, Farrar NJ, Shoeib M, Jones KC, Gobas FA. Characterization of polymer coated glass as a passive air sampler for persistent organic pollutants. Environ Sci Technol 2003;37:2486-93.
22. Wania F, Shen L, Lei YD, Teixeira C, Muir DCG. Development and calibration of a resin-based passive sampling system for monitoring persistent organic pollutants in the atmosphere. Environ Sci Technol 2003;37:1352-9.
23. Müller JF, Hawker DW, Connell DW, Kömp P, Mclachlan MS. Passive sampling of atmospheric SOCs using tristearin-coated fibreglass sheets. Atmos Environ 2000;34:3525-34.
24. Hellström A, Kylin H, Strachan WM, Jensen S. Distribution of some organochlorine compounds in pine needles from Central and Northern Europe. Environ Pollut 2004;128:29-48.
25. Hwang H, Wade TL, Sericano JL. Concentrations and source characterization of polycyclic aromatic hydrocarbons in pine needles from Korea, Mexico, and United States. Atmos Environ 2003;37:2259-67.
26. Tremolada P, Burnett V, Calamari D, Jones K. A study of the spatial distribution of PCBs in the UK atmosphere using pine needles. Chemosphere 1996;32:2189-203.
27. Gerdol R, Bragazza L, Marchesini R, et al. Use of moss (Tortula muralis Hedw.) for monitoring organic and inorganic air pollution in urban and rural sites in Northern Italy. Atmos Environ 2002;36:4069-75.
28. Lead WA, Steinnes E, Jones KC. Atmospheric deposition of PCBs to moss (Hylocomium splendens) in Norway between 1977 and 1990. Environ Sci Technol 1996;30:524-30.
29. Ockenden WA, Steinnes E, Parker C, Jones KC. Observations on persistent organic pollutants in plants: implications for their use as passive air samplers and for POP cycling. Environ Sci Technol 1998;32:2721-6.
30. Schramm KW. Hair: a matrix for non-invasive biomonitoring of organic chemicals in mammals. Bull Environ Contam Toxicol 1997;59:396-402.
31. Jaspers VL, Voorspoels S, Covaci A, Eens M. Can predatory bird feathers be used as a non-destructive biomonitoring tool of organic pollutants? Biol Lett 2006;2:283-5.
32. Zhang H, Chai Z, Sun H. Human hair as a potential biomonitor for assessing persistent organic pollutants. Environ Int 2007;33:685-93.
33. Iglesias-González A, Hardy EM, Appenzeller BMR. Cumulative exposure to organic pollutants of French children assessed by hair analysis. Environ Int 2020;134:105332.
34. Behrooz R, Poma G, Covaci A. Assessment of persistent organic pollutants in hair samples collected from several Iranian wild cat species. Environ Res 2020;183:109198.
35. Iatrou EI, Tsygankov V, Seryodkin I, et al. Monitoring of environmental persistent organic pollutants in hair samples collected from wild terrestrial mammals of Primorsky Krai, Russia. Environ Sci Pollut Res Int 2019;26:7640-50.
36. Covaci A, Tutudaki M, Tsatsakis AM, Schepens P. Hair analysis: another approach for the assessment of human exposure to selected persistent organochlorine pollutants. Chemosphere 2002;46:413-8.
37. D'Havé H, Covaci A, Scheirs J, Schepens P, Verhagen R, De Coen W. Hair as an indicator of endogenous tissue levels of brominated flame retardants in mammals. Environ Sci Technol 2005;39:6016-20.
38. Altshul L, Covaci A, Hauser R. The relationship between levels of PCBs and pesticides in human hair and blood: preliminary result. Environ Health Perspect 2004;112:1193-9.
39. Covaci A, Schepens P. Chromatographic aspects of the analysis of selected persistent organochlorine pollutants in human hair. Chromatographia 2001;53:S366-71.
40. Dauwe T, Jaspers V, Covaci A, Schepens P, Eens M. Feathers as a nondestructive biomonitor for persistent organic pollutants. Environ Toxicol Chem 2005;24:442-9.
41. Kočan A, Bencko V, Sixl W. Polychlorinated Dibenzo-p-dioxins (PCDDs) and Dibenzofurans (PCDFs) in the hair of people living on municipal refuse dumping sites in Cairo (Egypt). Toxicol Environ Chem 1992;36:33-7.
42. Tirler W, Voto G, Donega M. PCDD/F, PCB and hexachlorobenzene levels in hair. Organohalogen Compd 2001;52:290-2.
43. Gevao B, Al-bahloul M, Al-ghadban AN, et al. Polybrominated diphenyl ethers in indoor air in Kuwait: Implications for human exposure. Atmos Environ 2006;40:1419-26.
44. Gevao B, Boyle EA, Carrasco GG, Ghadban AN, Zafar J, Bahloul M. Spatial and temporal distributions of polycyclic aromatic hydrocarbons in the Northern Arabian Gulf sediments. Mar Pollut Bull 2016;112:218-24.
45. Gevao B, Helaleh M, Udin S, et al. Spatial and temporal distribution of persistent organic pollutants (POPs) in coastal marine sediments in Kuwait. Kuwait Institute for Scientific Research 2008; doi: 10.1016/j.chemosphere.2005.05.030.
46. Covaci A. Determination of brominated flame retardants, with emphasis on polybrominated diphenyl ethers (PBDEs) in environmental and human samples—a review. Environ Int 2003;29:735-56.
47. Jaward FM, Farrar NJ, Harner T, Sweetman AJ, Jones KC. Passive air sampling of PCBs, PBDEs, and organochlorine pesticides across Europe. Environ Sci Technol 2004;38:34-41.
48. Shoeib M, Harner T. Characterization and comparison of three passive air samplers for persistent organic pollutants. Environ Sci Technol 2002;36:4142-51.
49. Gevao B, Al-Bahloul M, Al-Ghadban AN, et al. House dust as a source of human exposure to polybrominated diphenyl ethers in Kuwait. Chemosphere 2006;64:603-8.
50. Sjödin A, Jakobsson E, Kierkegaard A, Marsh G, Sellström U. Gas chromatographic identification and quantification of polybrominated diphenyl ethers in a commercial product, Bromkal 70-5DE. J Chromatogr A 1998;822:83-9.
51. Bruckman P, Wackhe K, Ball M, Lis A, Papke O. . Degassing of PBBDD/PBDF levels from a television set-PBBDD/PBDF levels after a fire in a stock house-two case studies. Skoklester: Workshop on brominated flame retardants; 1998.
52. Ball M, Paepke O, Lis A. . Continuation of studies on formation of polybrominated dioxins and furans during subjecting flame protected plastics and textiles to thermal strain. Partial objective 1. Germany: Federal Environmental Agency; 1991.
53. Toriba A, Kuramae Y, Chetiyanukornkul T, et al. Quantification of polycyclic aromatic hydrocarbons (PAHs) in human hair by HPLC with fluorescence detection: a biological monitoring method to evaluate the exposure to PAHs. Biomed Chromatogr 2003;17:126-32.
54. Gill U, Covaci A, Ryan JJ, Emond A. Determination of persistent organohalogenated pollutants in human hair reference material (BCR 397): an interlaboratory study. Anal Bioanal Chem 2004;380:924-9.
55. Nakao T, Aozasa O, Ohta S, Miyata H. Assessment of human exposure to PCDDs, PCDFs and Co-PCBs using hair as a human pollution indicator sample I: development of analytical method for human hair and evaluation for exposure assessment. Chemosphere 2002;48:885-96.
56. Neuber K, Merkel G, Randow FF. Indoor air pollution by lindane and DDT indicated by head hair samples of children. Toxicol letters 1999;107:189-92.
57. Tsatsakis A, Tutudaki M. Progress in pesticide and POPs hair analysis for the assessment of exposure. Forensic Sci Int 2004;145:195-9.
58. Ostrea EM Jr, Villanueva-Uy E, Bielawski DM, et al. Maternal hair--an appropriate matrix for detecting maternal exposure to pesticides during pregnancy. Environ Res 2006;101:312-22.
59. Oghami T, Nonaka S, Irifune H, et al. A comparative study on polychlorinated biphenyl biphenyls (PCB) and polychlorinated quaterphenyls (PCQ) concentrations in subcuteneous fat tissue blood and hair of patients with Yusho in Nagasaki Perfecture. Fukukoa Acta Medica 1991;82:295-9.
60. Miekeley N, Diascarneiro M, Portodasilveira C. How reliable are human hair reference intervals for trace elements? Sci Total Environ 1998;218:9-17.
61. Steindel SJ, Howanitz PJ. The uncertainty of hair analysis for trace metals. JAMA 2001;285:83-5.
Cite This Article
Gevao B, Uddin S, Al-Bahloul M, Al-Mutairi A. Persistent organic pollutants on human and sheep hair and comparison with POPs in indoor and outdoor air. J Environ Expo Assess 2022;1:5. http://dx.doi.org/10.20517/jeea.2021.06
Gevao B, Uddin S, Al-Bahloul M, Al-Mutairi A. Persistent organic pollutants on human and sheep hair and comparison with POPs in indoor and outdoor air. Journal of Environmental Exposure Assessment. 2022; 1(1): 5. http://dx.doi.org/10.20517/jeea.2021.06
Gevao, Bondi, Saif Uddin, Majid Al-Bahloul, Ahmad Al-Mutairi. 2022. "Persistent organic pollutants on human and sheep hair and comparison with POPs in indoor and outdoor air" Journal of Environmental Exposure Assessment. 1, no.1: 5. http://dx.doi.org/10.20517/jeea.2021.06
Gevao, B.; Uddin S.; Al-Bahloul M.; Al-Mutairi A. Persistent organic pollutants on human and sheep hair and comparison with POPs in indoor and outdoor air. J. Environ. Expo. Assess. 2022, 1, 5. http://dx.doi.org/10.20517/jeea.2021.06
Comments must be written in English. Spam, offensive content, impersonation, and private information will not be permitted. If any comment is reported and identified as inappropriate content by OAE staff, the comment will be removed without notice. If you have any queries or need any help, please contact us at firstname.lastname@example.org.