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Int. J. Environ. Res. Public Health 2014, 11(3), 2642-2656; doi:10.3390/ijerph110302642
Published: 4 March 2014
Abstract: The upper layer of forest soils (0–20 cm depth) were collected from urban, suburban, and rural areas in the Pearl River Delta of Southern China to estimate the distribution and the possible sources of polycyclic aromatic hydrocarbons (PAHs). Total concentrations of PAHs in the forest soils decreased significantly along the urban–suburban–rural gradient, indicating the influence of anthropogenic emissions on the PAH distribution in forest soils. High and low molecular weight PAHs dominated in the urban and rural forest soils, respectively, implying the difference in emission sources between the areas. The values of PAH isomeric diagnostic ratios indicated that forest soil PAHs were mainly originated from traffic emissions, mixed sources and coal/wood combustion in the urban, suburban and rural areas, respectively. Principal component analysis revealed that traffic emissions, coal burning and residential biomass combustion were the three primary contributors to forest soil PAHs in the Pearl River Delta. Long range transportation of PAHs via atmosphere from urban area might also impact the PAHs distribution in the forest soils of rural area.
Polycyclic aromatic hydrocarbons (PAHs) are a group of organic contaminants which exist ubiquitously in the environment. Environmental PAHs come from two sources: natural processes (e.g., forest fires, volcanic activity, etc.) contributing to the background values of PAHs, and anthropogenic activities (e.g., incomplete combustion of fossil fuels, coke production, industrial processes, etc.) contributing to the contamination levels of PAHs [1,2,3,4]. Owing to their carcinogenic, mutagenic, and teratogenic effects on organisms, 16 PAHs were specified as priority control target pollutants by the United States Environmental Protection Agency (EPA) [5,6]. Given the increase of widespread extensive concerns about the environmental behavior and the human toxicity of PAHs, global monitoring of the levels and distribution of PAHs in soils is necessary for risk assessment on human health [4,7,8].
Once emitted, PAHs could be widely dispersed in the air, water and could be retained in the soil matrix for a long time after adsorption onto the soil organic matter . Soils and sediments are often the ultimate repository for most of the hydrophobic organic contaminants such as PAHs bonded with particles . It has been well documented that most anthropogenic PAHs will be restricted to the top layer of the soils .
As the biggest developing country, China has been estimated having annual total PAHs emissions of 25,300 tons , contributing over 20% of the global PAH emissions . The emitted PAHs mainly originate from the combustion of fossil fuels and biomass [14,15]. Recently, investigation on PAH concentrations and distribution in atmosphere, water, soils and sediments has been done at different regional scales in China [2,4,8]. As the primary PAH sink in terrestrial ecosystems , soils in many areas in China, for example the Pearl River Delta (PRD) , the Yangtze River Delta [4,17], and Beijing-Tianjin Area , contain the vast majority of PAHs. However, investigation on the concentrations, distribution and possible sources of PAHs in forest soils has been relatively less frequent than in urban and agricultural soils. Compared with common soils, forests soils inevitably have lower PAH levels owing to the effects of the forest canopy. Forest soil is one of the main components of multi-media including atmosphere, plant leaves, soil and runoff [19,20,21]. It has been estimated that forest ecosystems can play vital role in scavenging anthropogenic PAHs . As one of vital components, forest soils act as primary reservoirs of PAHs. The role of forest soils in sequestering PAHs should also be intensively considered. Therefore, the research on the distribution and the possible contributors of PAHs in differently disturbed forest soils was very necessary in assessing forest sequestration and in managing forest risks associated with exposure to these chemicals in soils.
The environment of the PRD, the most industrialized and urbanized region in southern China, has deteriorated severely during the past decades . Organic contaminants including PAHs, polychlorinated biphenyls, and organochlorine pesticides have been well documented in various environments in this region [8,16,23,24,25]. The objectives of this study were to: (1) Investigate the concentrations and profiles of PAHs in forest soils influenced by urbanization; (2) explore the possible sources of PAHs in the forest soils along an urban–rural gradient in the PRD.
2. Materials and Methods
2.1. Site Description and Soil Sampling
The PRD includes nine districts covering an area of about 4.2 × 104 km2 in Guangdong Province. The annual average temperature is 21–23 °C and ranges from 13–15 °C in January to 28–29 °C in July. The annual precipitation fluctuates between 1,500 and 1,800 mm with about 80% falling in the wet season from April to September .
According to previous studies , three forest sites representing different disturbances due to urbanization were selected for soil sampling in this study. In order to estimate PAH pollution over the whole region, we selected three moderately polluted sites rather than extreme sites. The urban site was Baiyunshan forest park (23°10′ N, 113°17′ E) in Guangzhou City, the suburban site was Liuxihe National Forest Park (23°32′ N, 113°45′ E) in Chonghua City, and the rural site was Yunjishan Nature Reserve (24°05′ N, 114°08′ E) in Xinfeng City. A total of 45 surface soil (0–20 cm depth) samples from each site were collected from July to August 2013. In order to avoid the influence of point source pollution, sampling spots were chosen away from roads and other emission sources.
Each sample comprises a mixture of soils containing more than five subsamples within 100 m2 and every sample site spacing is more than 50 m. After being transported to the laboratory, these soil samples were air dried, ground to pass through a 2-mm sieve, homogenized, and stored at 4 °C for analysis.
2.2. Chemicals and Materials
The priority 16 PAHs, including naphthalene (NAP), acenaphthene (ACE), acenaphthylene (ACY), fluorine (FLO), phenanthrene (PHE), anthracene (ANT), fluoranthene (FLA), pyrene (PYR), benz[a]anthracene (BaA), chrysene (CHR), benzo[b]fluoranthene (BbF), benzo[k]fluoranthene (BkF), benzo[a]pyrene (BaP), dibenz[a,h]anthracene (DahA), indeno[1,2,3-cd]pyrene (IcdP), and benzo[ghi]perylene (BghiP) (specified by EPA Method 610), in a mixture and a surrogate consisting of naphthalene-d8, acenaphthene-d10, phenanthrene-d10, chrysene-d12, and perylene-d12, as well as the native standards, were obtained from Ultra Scientific Inc. (North Kingston, RI, USA). Internal standards (hexamethylbenzene) were attained initially as a solid of 99% purity (Aldrich Chemicals, Gillingham, Dorset, UK). The PAH standard reference material (SRM 1491a) was purchased from the National Institute of Standards and Technology (NIST, Gaithersburg, MD, USA). All organic solvents (Nanjing Chemical Reagent Co., Nanjing, China) used in the extraction were redistilled using a glass system.
2.3. Sample Extraction
A 10 g soil sample spiked with 2.5 ng of each deuterated PAHs was mixed with 10 g of anhydrous sodium sulfate and then Soxhlet extracted for 24 h with 200 mL of hexane/acetone (1:1 v/v). The extracts were concentrated to 2 mL by rotary vacuum evaporation and solvent-exchanged to hexane. The concentrated extracts were cleaned by silica gel column chromatography (25 cm × 1 cm i.d). The glass chromatographic column fitted with a Teflon stopcock was packed from the bottom with glass wool followed by 10 g of activated silica and then 2 cm of anhydrous sodium sulfate. After transferring the sample extract, the column was eluted with 25 mL of n-hexane and 35 mL of n-hexane/DCM (3:2, v/v), respectively. The first fraction containing n-alkanes was discarded and the second fraction containing PAHs was collected. Afterward, the collected PAHs fraction was vacuum-evaporated, solvent exchanged to isooctane, and then concentrated to 0.2 mL under a gentle stream of nitrogen before GC/MS analysis.
2.4. GC Analysis and Quantification
The determination of PAHs was performed on an Agilent 6890 N gas chromatograph-5973 mass selective detector (GC-MSD) system (Agilent Technologies Inc., Santa Clara, CA, USA) equipped with a fused silica capillary HP-5MS column (30 m × 0.25 mm × 0.25 mm). The carrier gas was helium at a constant flow rate of 1.5 mL∙min−1. The column temperature was programmed to rise from 70 to 200 °C at 3 °C∙min−1 and then to 285 °C at 5 °C∙min−1 and held for 12 min at 280 °C. A 1 μL sample was injected in splitless mode. The interface, ion source, and quadrupole temperatures were maintained at 280, 150, and 160 °C, respectively. The ionization was carried out in the electron impact mode at 70 eV and the data were acquired under selected ion monitoring (SIM) mode. Identification of PAHs was based on the selected ions and the comparison of retention time between samples and the standard solution containing individual PAHs. The quantitation of PAH was done by using relative response factor of target PAHs to internal standards. For target PAHs, one or more quantitation ions and confirmation ions were used.
2.5. Quality Control
The instrument was calibrated daily with calibration standards and the relative percentage difference between the four-point calibration and daily calibration was less than 20%. Method blanks (solvent), spiked blanks (standards spiked into the solvent), sample duplicates, and a sample from the National Institute of Standards and Technology standard reference material (NIST 1941b) were analyzed routinely with field samples. In addition, the surrogate standards were added to all the samples (including quality assessment samples) to monitor procedural performance. The surrogate recoveries (%) in field samples were as follows: naphthalene-d8 = 47.2 ± 7.5; acenaphthene-d10 = 81.3 ± 4.4; phenanthrene-d10 = 96.3 ± 3.9; chrysene-d12 = 92.8 ± 6.7; and perylene-d12 = 96.6 ± 5.8.The method detect limit (MDL) was calculated to be in the range of 0.6–2.6 ng∙g−1 DW using the Method Detection Limit Calculator . The PAH concentrations in this study are presented on a dry weight basis.
2.6. Statistical Analysis
Statistical analyses including one-way analysis of variance (ANOVA), correlation analysis, and principal component analysis (PCA) were performed using SPSS 17.0 for Windows (SPSS Inc., Chicago, IL, USA). The concentrations of PAHs were log-transformed to achieve normal distribution prior to the statistical analysis.
3. Results and Discussion
3.1. PAH Concentrations
Concentrations of total PAHs (ΣPAHs) in the 45 forest soil samples from the urban, suburban, and rural areas ranged from 71.28 to 515.34, 39.85 to 201.01, and 18.90 to 75.17 ng∙g−1, respectively (Table 1). As expected, PAHs concentrations showed a strong urban–suburban–rural gradient. The distribution pattern of ΣPAHs indicated a significant influence of urbanization on forest soils. According to the results shown in Table 1, the highest ΣPAHs was found in the urban forest area (152.10 ± 79.41 ng∙g−1, mean ± standard deviation (S.D.), as follows), and is comparable to the corresponding levels in the urban forest soils of Klang Valley, Malaysia (155.20 ± 91.40 ng∙g−1) . Compared to other soils in the PRD, e.g., the paddy fields (253.00 ± 130.00 ng∙g−1) , vegetable soils (318.20 ± 156.40 ng∙g−1) , crop soils (218.00 ± 123.00 ng∙g−1), and particularly the urban soils (960.00~1,800.00 ng∙g−1) [16,30], the ΣPAHs in urban forest soils in this study was significantly lower. The mean concentrations of ΣPAHs in suburban forest soils (73.67 ± 16.34 ng∙g−1) was about half of those in the urban area and double those in the rural area. Compared to suburban residential areas in the PRD, such as Guangzhou (160.00~1,300.00 ng∙g−1), Dongguan (128.00~357.00 ng∙g−1), and Shenzhen (230.00~3,700.00 ng∙g−1) [31,32], and agricultural soils in suburban areas around Guangzhou (422.00 ± 194.35 ng∙g−1), PAH concentrations in suburban forest soils were much lower. This comparison implied that urban forests could play important role in scavenging PAHs from the atmospheric deposition, which was consistent with the findings by Tian et al. (2008) . The concentrations of PAHs in the rural forest soils (35.86 ± 6.91 ng∙g−1) were similar to the rural areas around the world, for example, volcanic mountains in the subtropical Atlantic (33.70 ng∙g−1) , tropical regions like Ghana (31.20 ng∙g−1) , mountains of Western Canada (30.00 ng∙g−1) , and mountains of Pohang South Korea (25.60 ng∙g−1) .
|Table 1. Concentrations (ng∙g−1 dry weight) of PAHs in forest soils in urban, suburban, and rural areas.|
|R3 ≤ /R ≥ 4 c||0.41||0.14||1.53||1.30||0.41||2.33||2.46||0.38||3.34|
Note: a Total concentrations of 16 individual PAHs; b ∑PAH7c: concentrations of seven carcinogenic PAHs; c Ratio of sum concentration of low molecular weight PAHs (≤3 rings) to that of high molecular weight PAHs (≥4 rings).
According to the classification system suggested by Maliszewska-Kordybach , a soil concentration of 200–600 ng∙g−1 PAHs represents weak contamination and a concentration below 200 ng∙g−1 indicates no contamination. Compared with the results of other studies, the ΣPAHs of forest soils in this research fell within the range of low to middle levels. However, the concentrations of ΣPAHs in the rural area were much higher than those of endogenous sources (1–10 ng∙g−1) resulting from plant synthesis and natural fires , implying that anthropogenic PAHs from urban area might also contribute to the forest soils via atmospheric long-range transportation. None of the PAH concentrations of soil samples in this study were more than 600 ng∙g−1, and 17.8 and 4.4% of the samples in urban and suburban forest soils, respectively, were weakly contaminated.
3.2. PAH Profiles
The composition profiles of PAHs in the three areas are presented in Figure 1. The profile of high molecular weight PAHs (HMW-PAHs) decreased along urban–suburban–rural transect, e.g., 6-ringed PAHs comprised from 12.5% of ΣPAHs in the urban areas to 4.8% in the rural areas, whereas the fractions of low molecular weight PAHs (LMW-PAHs, including 2- and 3-ringed PAHs) increased along the gradient with 2-ringed PAHs from 13.5 to 39.0% and 3-ringed PAHs from 15.1 to 32.6%.
Figure 1 also showed that HMW-PAHs dominated in the urban forest soils while LMW-PAHs dominated in suburban and rural soils. Interestingly, the dominance of 2, 3-ringed PAHs was also found in less polluted soils such as tropical [39,40] and mountain soils , whereas 4-6-ringed PAHs dominated the composition in urban soils [41,42,43,44,45]. Additionally, the composition and the relative abundance of individual PAHs varied considerably.
Figure 2 shows that the percentages of individual PAHs to ΣPAHs in our soil samples. NAP was the most dominant component, representing 16.1%, 26.4%, and 33.1% of ΣPAHs in urban, suburban, and rural sites, respectively. NAP, PHE, ANT, FLA, and PYR were dominant components, which account for 55.8% and 65.3% to ΣPAHs in urban and suburban sites, respectively. NAP and PHE were dominant components in rural site with 53.3% of percentage to ΣPAHs.
Emission sources as well as long range transportation of PAHs via atmosphere contribute greatly the composition profiles of environmental PAHs . The urban–suburban–rural gradient of composition profiles might be ascribed to different emissions. As well known, LMW-PAHs were chiefly generated by low- or moderate-temperature combustion process (such as biomass combustion and domestic coal burning) while HMW-PAHs were mainly generated by high-temperature combustion process (such as vehicular exhausts and industrial coal combustion). In the urban areas, there were usually much devise of emissions (traffic, industrial, etc.) than in the rural ones. The larger fraction of LMW-PAHs in the rural forest soils in this study indicated that PAHs might mainly stem from low- or moderate-temperature combustion processes. The higher fraction of HMW-PAHs (49.1%–74.7%) in the urban forest soils implied that there were additional industrial emissions contributing to soil PAHs. As demonstrated by numerous researchers, traffic and industrial emissions were the main contributors to atmospheric PAHs in particulates at the urban centers and at the locations close to major highways [47,48,49], so we inferred that industrial and traffic emissions have caused significant accumulation of PAHs in the urban forest soils, while atmospheric transportation and deposition of pyrogenic–stemmed PAHs also contributed to the forest soils PAHs at rural areas. Some PAHs, such as Nap, might be emitted by biogenic sources, in particular at forest sites , which partly explained the dominance of LMW-PAHs at the rural site (Figure 1 and Figure 2). Furthermore, in rural areas, coal burning and biomass combustion are the major sources of PAH contamination, and the emission factors for low-ringed PAHs from biomass burning are higher than those for coal combustion . Additionally, there is more photochemical degradation of LMW PAHs in urban areas than in rural villages because of OH radicals , which further explained why higher concentrations of 2,3-ringed PAHs existed in the rural village area than in the urban area. The urban–suburban–rural gradient obtained in this research verified the differences in emission sources.
3.3. Source Apportionment by Isomeric Ratios of PAHs
The anthropogenic release of PAHs can be attributed to petrogenic and pyrogenic origins. The PAHs of petrogenic origins are characterized by the predominance of 2- and 3-ringed PAHs, while the PAHs from pyrogenic origins are characterized by a high proportion of PAHs with more than four rings. Beside the ratio of LMW- and HMW-PAHs to total PAHs, several PAH congener ratios, such as Ant/(Phe + Ant), Fla/(Fla + Pyr), Phe/(Phe + Ant), BaA/(BaA + Chr), Flu/(Flu + Pyr), and InP/(InP + BP), have been widely used to distinguish the possible source categories of environmental PAHs [51,52,53].
A ratio of Ant/(Ant + Phe) < 0.1 is indicative of a petroleum source, while a ratio > 0.1 is indicative of combustion. Meanwhile, a ratio of Fla/(Fla + Pyr) lower than 0.40 indicates a petroleum source and one higher than 0.50 indicates a biomass and coal combustion sources, while a ratio between 0.4 and 0.5 is characteristic of liquid fossil fuel combustion. A ratio of IcdP/(IcdP + BghiP) lower than 0.20 indicates a petroleum source, one higher than 0.50 indicates biomass and coal combustion sources, and one between 0.20 and 0.50 indicates liquid fossil fuel combustion . Moreover, a ratio of BaA/(BaA + Chr) less than 0.2 suggests a petroleum source, 0.2–0.35 suggests petroleum combustion (especially liquid fossil fuel, vehicle and crude oil), and a ratio greater than 0.35 suggests combustion of coal, grass, and wood [54,55].
In the present study, the ratios of Ant/(Ant + Phe) varies between 0.11 and 0.29 in forest soils, and the ratios of Fla/(Fla + Pyr) were higher than 0.4. In addition, 48.9 and 15.6% of the ratios of Fla/(Fla + Pyr) were 0.4–0.5 in the urban and suburban forest soils, respectively (Figure 3a). However, the ratios of Fla/(Fla + Pyr) were more than 0.5 in rural forest soils. The IcdP/(IcdP + BghiP) ratios changed from 0.37 to 0.71 in all of the forest samples, and samples from rural forest soils had ratios above 0.5. Furthermore, 60.0 and 84.4% of the IcdP/(IcdP + BghiP) ratios were above 0.50 in urban and suburban forest soils, respectively, while 40.0 and 15.6% of the IcdP/(IcdP + BghiP) ratios varied between 0.2 and 0.5 in urban and suburban forest soils, respectively. The ratios of BaA/(BaA + Chr) varied from 0.28 to 0.51, with most of them higher than 0.35 (Figure 3b). The above ratio values implied that traffic emission and coal combustion might contribute to the occurrence of PAHs in urban forest soils, while biomass- and coal-related residential heating might contribute to the forest soil PAHs at rural area. The results were similar to previous reports from the urban soils in the PRD [25,32,56,57].
3.4. Source Identification by Principal Component Analysis
Principal component analysis (PCA) was conducted to reduce the set of original variables and to extract a small number of latent factors for analyzing the relationship among the observed variables for further investigations of possible sources of PAHs. Two principal components (PC1and PC2) were extracted with eigenvalues > 1, accounting for the majority (>85%) of the total variances (Table 2) at the three forest soils.
As well known, LMW-PAHs such as PHE, ANT, and FLO are indicative of coke oven origin , NAP accounts for the majority of the mass in coke oven, highway tunnel, and gasoline engine samples , and ACY and ACE are markers for domestic wood combustion . On the other hand, HMW-PAHs such as FLA, PYR, BaA, CHR, BbF, BkF, BaP, IcdP, DahA, and BghiP are typical markers for pyrolysis or incomplete combustion. FLA, PYR, BaA, CHR, and BaP are markers for coal combustion [56,57,58]. BbF and BkF are components of fossil fuels and portions of them are associated with their combustion . BaA and CHR often result from the combustion of both diesel and natural gas [59,60]. IcdP, BghiP, and DahA are associated with traffic emission .
|Table 2. Principal component analysis after Varimax rotation for the selected PAHs in forest soils in urban, suburban, and rural sites. Only factors with loading values greater than 0.5 were listed.|
|Pollution source||Traffic emission||Coal combustion||Coal and biomass combustion||Traffic emission||Biomasscom
PC1 explained 79.49, 63.41, and 72.67% of total variances in forest soils in urban, suburban, and rural sites, respectively (Table 2). It was characterized by high loadings of 4-6-ringed PAHs, including BaP, IcdP, DahA, BghiP, and PYR, and moderate loadings of FLA, BaA, CHR, BbF, and BkF in urban forest soils. Suburban forest soils were characterized by loadings of 3-6-ringed PAHs, including NAP, ACY, ACE, ANT, FLA, PYR, BaA, and BaP, and moderate loadings of FLO, PHE, FLA and PYR. Rural forest soils were characterized by main loadings of 2,3- and 6-ringed PAHs, including NAP, ACE, FLO, PHE,ANT, FLA, IcdP, DahA, and BghiP. Consequently, PC1 reflected a pyrogenic source (traffic emission) of PAHs in the urban forest soils. The origin of PAHs in suburban forest soils can be attributed to a pyrogenic (coal combustion) source, while the PAHs in rural forest soils mainly originated from wood and coal combustion sources.
PC2 accounted for 8.10, 27.47, and 13.32% of total variances in urban, suburban, and rural sites, respectively (Table 2). It was dominated by LMW-PAHs, such as NAP, ACY, ACE, FLO, PHE, and ANT in urban soils, indicating mixed sources of petroleum and low temperature combustion in those areas. Suburban sites were dominated by HMW-PAHs, such as FLO, PHE, BbF, BkF, IcdP, DahA, and BghiP, which indicated traffic emission and coke oven origins. In contrast, rural forest soils were dominated by HMW-PAHs such as PYR, BaA, CHR, BbF, and BkF, indicating that coal combustion may be the source of PAHs in rural sites.
These results are also in agreement with previous observations by Cai et al. and Liu et al. in urban soils [8,16]. Mixed sources (traffic emission, biomass and coal combustion) contributed to the suburban sites, and residential emissions were the dominant source at rural sites [43,62], which is in accordance with our results.
Concentrations of PAHs in forest soils showed a strong urban–suburban–rural gradient, with total concentrations up to four times higher in urban areas than in rural ones. HMW-PAHs and LMW-PAHs dominated in the urban forest soils and rural forest soils, respectively. The composition profiles of PAHs displayed an urban–suburban–rural gradient owing to the emission sources, implying the influence of urbanization on the distribution of PAHs in forest soils. The isomeric diagnostic ratios of PAHs revealed that forest soil PAHs were mainly originated from traffic emission, mixed sources and coal/wood combustion in the urban, suburban and rural areas, respectively. Traffic emission, coal combustion and residential biomass emission were the three primary contributors to forest soil PAHs in the PRD. Forest soils in the urban and suburban areas of PRD were weakly contaminated by PAHs. Long range transportation via atmosphere from urban area can also impact forest soils in rural area.
This work was supported by the Special Research Program of the Research Institute for Tropical Forestry, CAF (No. RITFYW2X201104), and the Program of Forest Ecological Benefits Monitoring Network in Guang Zhou (2013–2014). The study was also supported by the CFERN and GENE Award Funds for ecological papers.
Fuchun Tong, Yuanwen Kuang and Bufeng Chen were all involved in conceptualizing, designing, and implementing the project; in addition to providing revisions and feedback on the manuscript by Yihua Xiao and Yuanwen Kuang. Yihua Xiao carried out all data collection and drafted the manuscript.
Conflicts of Interest
The authors declare no conflict of interest.
- Zohair, A.; Salim, A.B.; Soyibo, A.A.; Beek, A.J. Residues of polycyclic aromatic hydrocarbons (PAHs), polychlorinated biphenyls (PCBs) and organochlorine pesticides in organically-farmed vegetables. Chemosphere 2006, 63, 541–553. [Google Scholar] [CrossRef]
- Peng, C.; Chen, W.P.; Liao, X.L.; Wang, M.L.; Ouyang, Z.Y.; Jiao, W.T. Polycyclic aromatic hydrocarbons in urban soils of Beijing: Status, sources, distribution and potential risk. Environ. Pollut. 2011, 159, 802–810. [Google Scholar] [CrossRef]
- Mastral, A.M.; Callen, M.S. A review on polycyclic aromatic hydrocarbon (PAH) emissions from energy generation. Environ. Sci. Technol. 2000, 34, 3051–3057. [Google Scholar] [CrossRef]
- Wang, X.T.; Miao, Y.; Zhang, Y.; Li, Y.C.; Wu, M.H.; Yu, G. Polycyclic aromatic hydrocarbons (PAHs) in urban soils of the megacity Shanghai: Occurrence, source apportionment and potential human health risk. Sci. Total. Environ. 2013, 447, 80–89. [Google Scholar] [CrossRef]
- Finlayson-Pitts, B.J.; Pitts, J.N. Tropospheric air pollution: Ozone, airborne toxics, polycyclic aromatic hydrocarbons, and particles. Science 1997, 276, 1045–1051. [Google Scholar] [CrossRef]
- Okona-Mensah, K.B.; Battershill, J.; Boobis, A.; Fielder, R. An approach to investigating the importance of high potency polycyclic aromatic hydrocarbons (PAHs) in the induction of lung cancer by air pollution. Food Chem. Toxicol. 2005, 43, 1103–1116. [Google Scholar] [CrossRef]
- Ravindra, K.; Sokhi, R.; Van Grieken, R. Atmospheric polycyclic aromatic hydrocarbons: Source attribution, emission factors and regulation. Atmos. Environ. 2008, 42, 2895–2921. [Google Scholar] [CrossRef]
- Liu, G.; Yu, L.; Li, J.; Liu, X.; Zhang, G. PAHs in soils and estimated air–soil exchange in the Pearl River Delta, south China. Environ. Monit. Assess. 2011, 173, 861–870. [Google Scholar] [CrossRef]
- Huang, W.L.; Ping, P.A.; Yu, Z.Q.; Fu, H.M. Effects of organic matter heterogeneity on sorption and desorption of organic contaminants by soils and sediments. Appl. Geochem. 2003, 18, 955–972. [Google Scholar] [CrossRef]
- Wild, S.R.; Jones, K.C. Polynuclear aromatic hydrocarbons in the United Kingdom environment: A preliminary source inventory and budget. Environ. Pollut. 1995, 88, 91–108. [Google Scholar] [CrossRef]
- Culotta, L.; Stefano, C.D.; Gianguzza, A.; Mannino, M.R.; Orecchio, S. The PAH composition of surface sediments from stagnone coastal lagoon, Marsala (Italy). Mar. Chem. 2006, 99, 117–127. [Google Scholar] [CrossRef]
- Xu, S.S.; Liu, W.X.; Tao, S. Emission of polycyclic aromatic hydrocarbons in China. Environ. Sci. Technol. 2006, 40, 702–708. [Google Scholar] [CrossRef]
- Zhang, Y.X.; Tao, S. Global atmospheric emission inventory of polycyclic aromatic hydrocarbons (PAHs ) for 2004. Atmos. Environ. 2008, 43, 812–819. [Google Scholar] [CrossRef]
- Zhang, Y.X.; Tao, S.; Cao, J.J.; Coveney, R.M. Emission of polycyclic aromatic hydrocarbons in China by county. Environ. Sci. Technol. 2007, 41, 683–687. [Google Scholar] [CrossRef]
- Wang, C.; Wang, X.; Gong, P.; Yao, T. Polycyclic aromatic hydrocarbons in surface soil across the Tibetan Plateau: Spatial distribution, source and air–soil exchange. Environ. Pollut. 2014, 184, 138–144. [Google Scholar] [CrossRef]
- Cai, Q.Y.; Mo, C.H.; Li, Y.H.; Zeng, Q.Y.; Katsoyiannis, A.; Wu, Q.T.; Ferard, J.F. Occurrence and assessment of polycyclic aromatic hydrocarbons in soils from vegetable fields of the Pearl River Delta, south China. Chemosphere 2007, 68, 159–168. [Google Scholar] [CrossRef]
- Yin, C.Q.; Jiang, X.; Yang, X.L.; Bian, Y.R.; Wang, F. Polycyclic aromatic hydrocarbons in soils in the vicinity of Nanjing, China. Chemosphere 2008, 73, 389–394. [Google Scholar] [CrossRef]
- Zuo, Q.; Duan, Y.H.; Yang, Y.; Wang, X.J.; Tao, S. Source apportionment of polycyclic aromatic hydrocarbons in surface soil in Tianjin, China. Environ. Pollut. 2007, 147, 303–310. [Google Scholar] [CrossRef]
- Orecchio, S. Assessment of polycyclic aromatic hydrocarbons (PAHs) in soil of a natural reserve (Isola delle Femmine) (Italy) located in front of a plant for the production of cement. J. Hazard. Mater. 2010, 173, 358–368. [Google Scholar] [CrossRef]
- Krauss, M.; Wilcke, W.; Martius, C.; Bandeira, A.G.; Garcia, M.V.; Amelung, W. Atmospheric versus biological sources of polycyclic aromatic hydrocarbons (PAHs) in a tropical rain forest environment. Environ. Pollut. 2005, 135, 143–154. [Google Scholar] [CrossRef]
- Jensen, H.; Reimann, C.; Finne, T.E.; Ottesen, R.T.; Arnoldussen, A. PAH-concentrations and compositions in the top 2 cm of forest soils along a 120 km long transect through agricultural areas, forests and the city of Oslo, Norway. Environ. Pollut. 2007, 145, 829–838. [Google Scholar] [CrossRef]
- Zhang, K.; Wei, Y.L.; Zeng, E.Y. A review of environmental and human exposure to persistent organic pollutants in the Pearl River Delta, south China. Sci. Total. Environ. 2013, 463, 1093–1110. [Google Scholar] [CrossRef]
- Statistical Bureau of Guangdong Province. Guangdong Year Book (1950–2011); Guangdong Publishing House: Guangzhou, China, 2011. [Google Scholar]
- Cai, Q.Y.; Mo, C.H.; Wu, Q.T.; Zeng, Q.Y.; Katsoyiannis, A.; Ferard, J.F. Bioremediation of polycyclic aromatic hydrocarbons (PAHs)𠄔Contaminated sewage sludge by different composting processes. J. Hazard. Mater. 2007, 142, 535–542. [Google Scholar] [CrossRef]
- Fu, J.; Mai, B.; Sheng, G.; Zhang, G.; Wang, X.; Peng, P.; Xiao, X.; Ran, R.; Cheng, F.; Peng, X.; et al. Persistent organic pollutants in environment of the Pearl River Delta, China: An overview. Chemosphere 2003, 52, 1411–1422. [Google Scholar] [CrossRef]
- Editorial Committee of Foresets of Guangdong. Guangdong Yearbook; Guangdong Yearbook Publishing House: Guangzhou, China, 2005; (in Chinese). [Google Scholar]
- Fang, Y.T.; Yoh, M.; Koba, K.; Zhu, W.X.; Takebayashi, Y.U.; Xiao, Y.H.; Lei, C.Y.; Mo, J.M.; Zhang, W.; Lu, X.K. Nitrogen deposition and forest nitrogen cycling along an Urban–Rural transect in southern China. Global Change Biol. 2011, 17, 872–885. [Google Scholar]
- Environmental Protection Agency (EPA) Method, 40 CFR Part 136, APPENDEX B. Available online: http://www.epa.gov/region9/qa/pdfs/40cfr136_03.pdf (accessed on 6 January 2014).
- Von Lau, E.; Gan, S.; Ng, H.K. Distribution and source apportionment of polycyclic aromatic hydrocarbons (PAHs) in surface soils from five different locations in Klang Valley, Malaysia. Bull. Environ. Contam. Toxicol. 2012, 88, 741–746. [Google Scholar]
- Hao, R.; Wan, H.F.; Song, Y.T.; Jiang, H.; Peng, S.L. Polycyclic aromatic hydrocarbons in agricultural soils of the southern subtropics, China. Pedosphere 2007, 17, 673–680. [Google Scholar] [CrossRef]
- Chen, L.; Ran, Y.; Xing, B.; Mai, B.; He, J.; Wei, X.; Sheng, G. Contents and sources of polycyclic aromatic hydrocarbons and organochlorine pesticides in vegetable soils of Guangzhou, China. Chemosphere 2005, 60, 879–890. [Google Scholar] [CrossRef]
- Zheng, T.H.; Ran, Y.; Chen, L. Polycyclic aromatic hydrocarbons (PAHs) in rural soils of Dongjiang river basin: Occurrence, source apportionment, and potential human health risk. J. Soil Sediment. 2013, 14, 1–11. [Google Scholar]
- Tian, X.; Liu, J.X.; Zhou, G.Y.; Peng, P.A.; Wang, X.L.; Wang, C.L. Estimation of the annual scavenged amount of polycyclic aromatic hydrocarbons by forests in the Pearl River Delta of southern China. Environ. Pollut. 2008, 156, 306–315. [Google Scholar] [CrossRef]
- Ribes, A.; Grimalt, J.O.; Garcia, C.J.; Cuevas, E. Polycyclic aromatic hydrocarbons in mountain soils of the subtropical Atlantic. J. Environ. Qual. 2003, 32, 977–987. [Google Scholar] [CrossRef]
- Wilcke, W. Polycyclic aromatic hydrocarbons (PAHs) in soil—A review. J. Plant. Nutr. Soil Sci. 2000, 163, 229–248. [Google Scholar] [CrossRef]
- Choi, S.D.; Shunthirasingham, C.; Daly, G.L.; Xiao, H.; Lei, Y.D.; Wania, F. Levels of polycyclic aromatic hydrocarbons in Canadian mountain air and soil are controlled by proximity to roads. Environ. Pollut. 2009, 157, 3199–3206. [Google Scholar] [CrossRef]
- Kim, E.J.; Oh, J.E.; Chang, Y.S. Effects of forest fire on the level and distribution of PCDD/Fs and PAHs in soil. Sci. Total Environ. 2003, 311, 177–189. [Google Scholar] [CrossRef]
- Maliszewska-Kordybach, B. Polycyclic aromatic hydrocarbons in agricultural soils in Poland: Preliminary proposals for criteria to evaluate the level of soil contamination. Appl. Geochem. 1996, 11, 121–127. [Google Scholar] [CrossRef]
- Wilcke, W.; Amelung, W.; Martius, C.; Garcia, V.B.; Zech, W. Biological sources of polycyclic aromatic hydrocarbons (PAHs) in the Amazonian rain forest. J. Plant. Nutr. Soil Sci. 2000, 163, 27–30. [Google Scholar] [CrossRef]
- Daly, G.L.; Lei, Y.D.; Castillo, L.E.; Muir, D.C.; Wania, F. Polycyclic aromatic hydrocarbons in costa rican air and soil: A tropical/temperate comparison. Atmos. Environ. 2007, 41, 7339–7350. [Google Scholar] [CrossRef]
- Tsibart, A.S.; Gennadiev, A.N. Polycyclic aromatic hydrocarbons in soils: Sources, behavior, and indication significance (a review). Eurasian Soil Sci. 2013, 46, 728–741. [Google Scholar] [CrossRef]
- Liu, Y.; Chen, L.; Zhao, J.F. Polycyclic aromatic hydrocarbons in the surface soil of Shanghai, China: Concentrations, distribution and sources. Org. Geochem. 2010, 41, 355–362. [Google Scholar] [CrossRef]
- Zhang, J.; Yang, J.C.; Wang, R.Q.; Hou, H.; Du, X.M.; Fan, S.K.; Liu, J.S.; Dai, J.L. Effects of pollution sources and soil properties on distribution of polycyclic aromatic hydrocarbons and risk assessment. Sci. Total. Environ. 2013, 463, 1–10. [Google Scholar]
- Wang, W.T.; Simonich, S.; Giri, B.; Chang, Y.; Zhang, Y.G.; Jia, Y.L.; Tao, S.; Wang, R.; Wang, B.; Li, W.; et al. Atmospheric concentrations and air–soil gas exchange of polycyclic aromatic hydrocarbons (PAHs) in remote, rural village and urban areas of Beijing–Tianjin region, north China. Sci. Total. Environ. 2011, 409, 2942–2950. [Google Scholar] [CrossRef]
- Wang, W.T.; Staci, L.; Massey, S.; Xue, M.; Zhao, J.Y.; Zhang, N.; Wang, R.; Cao, J.; Tao, S. Concentrations, sources and spatial distribution of polycyclic aromatic hydrocarbons in soils from Beijing, Tianjin and surrounding areas, north China. Environ. Pollut. 2010, 158, 1245–1251. [Google Scholar] [CrossRef]
- Sun, F.F.; Wen, D.Z.; Kuang, Y.Y.; Li, J.; Li, J.; Zuo, W. Concentrations of heavy metals and polycyclic aromatic hydrocarbons in needles of masson pine (Pinus massoniana L.) growing nearby different industrial sources. J. Environ. Sci. 2010, 22, 1006–1013. [Google Scholar] [CrossRef]
- Alfani, A.; de Nicola, F.; Maisto, G.; Prati, M.V. Long-term PAH accumulation after bud break in Quercus ilex L. leaves in a polluted environment. Atmos. Environ. 2005, 39, 307–314. [Google Scholar] [CrossRef]
- De Nicola, F.; Maisto, G.; Prati, M.V.; Alfani, A. Leaf accumulation of trace elements and polycyclic aromatic hydrocarbons (PAHs) in Quercus ilex L. Environ. Pollut. 2008, 153, 376–383. [Google Scholar] [CrossRef]
- Gunawardena, J.; Egodawatta, P.; Ayoko, G.A.; Goonetilleke, A. Role of traffic in atmospheric accumulation of heavy metals and polycyclic aromatic hydrocarbons. Atmos. Environ. 2012, 54, 502–510. [Google Scholar] [CrossRef]
- Wang, R.; Tao, S.; Wang, B.; Yang, Y.; Lang, C.; Zhang, Y.X.; Hu, J.; Ma, J.M.; Hung, H. Sources and pathways of polycyclic aromatic hydrocarbons transported to Alert, the Canadian High Arctic. Environ. Sci. Technol. 2009, 44, 1017–1022. [Google Scholar]
- Tay, C.K.; Biney, C.A. Levels and sources of polycyclic aromatic hydrocarbons (PAHs) in selected irrigated urban agricultural soils in Accra, Ghana. Environ. Earth Sci. 2013, 68, 1773–1782. [Google Scholar] [CrossRef]
- Zakaria, M.P.; Takada, H.; Tsutsumi, S.; Ohno, K.; Yamada, J.; Kouno, E. Distribution of polycyclic aromatic hydrocarbons (PAHs) in rivers and estuaries in Malaysia: A widespread input of petrogenic PAHs. Environ. Sci. Technol. 2002, 36, 1907–1918. [Google Scholar] [CrossRef]
- Yunker, M.B.; Macdonald, R.W.; Vingarzan, R.; Mitchell, R.H.; Goyette, D.; Sylvestre, S. PAHs in the Fraser River Basin: A critical appraisal of PAH ratios as indicators of PAH source and composition. Org. Geochem. 2002, 33, 489–515. [Google Scholar] [CrossRef]
- Wu, Y.L.; Wang, X.H.; Li, Y.Y.; Hong, H.S. Occurrence of polycyclic aromatic hydrocarbons (PAHs) in sea water from the western Taiwan Strait. China Mar. Pollut. Bull. 2011, 63, 459–463. [Google Scholar] [CrossRef]
- Magi, E.; Bianco, R.; Ianni, C.; Carro, M.D. Distribution of polycyclic aromatic hydrocarbons in the sediments of the Adriatic Sea. Environ. Pollut. 2002, 119, 91–98. [Google Scholar] [CrossRef]
- Ma, X.; Ran, Y.; Gong, J.; Zou, M. Concentrations and inventories of polycyclic aromatic hydrocarbons and organochlorine pesticides in watershed soils in the Pearl River Delta, China. Environ. Monit. Assess. 2008, 145, 453–464. [Google Scholar] [CrossRef]
- Lehndorff, E.; Schwark, L. Biomonitoring of air quality in the cologne conurbation using pine needles as a passive sampler-part II: Polycyclic aromatic hydrocarbons (PAH). Atmos. Environ. 2004, 38, 3793–3808. [Google Scholar] [CrossRef]
- Simcik, M.F.; Eisenreich, S.J.; Lioy, P.J. Source apportionment and source/sink relationships of PAHs in the coastal atmosphere of Chicago and Lake Michigan. Atmos. Environ. 1999, 33, 5071–5079. [Google Scholar] [CrossRef]
- Khalili, N.R.; Scheff, P.A.; Holsen, T.M. PAH source fingerprints for coke ovens, diesel and gasoline engines, highway tunnels, and wood combustion emission. Atmos. Environ. 1995, 29, 533–542. [Google Scholar] [CrossRef]
- Valavanidis, A.; Fiotakis, K.; Vlahogianni, T.; Bakeas, E.B.; Triantafillaki, S.; Paraskevopoulou, V.; Dassenakis, M. Characterization of atmospheric particulates, particle-bound transition metals and polycyclic aromatic hydrocarbons of urban air in the centre of Athens (Greece). Chemosphere 2006, 65, 760–768. [Google Scholar] [CrossRef]
- Kavouras, I.G.; Koutrakis, P.; Tsapakis, M.; Lagoudari, E.; Stephanou, E.G.; Baer, D.V.; Oyola, P. Source apportionment of urban particulate aliphatic and polynuclear aromatic hydrocarbons (PAHs) using multivariate methods. Environ. Sci. Technol. 2001, 35, 2288–2294. [Google Scholar] [CrossRef]
- Zeng, F.; Cui, K.; Xie, Z.; Wu, L.; Liu, M.; Sun, G.; Zeng, Z. Phthalate esters (PAEs): Emerging organic contaminants in agricultural soils in peri-urban areas around Guangzhou, China. Environ. Pollut. 2008, 156, 425–434. [Google Scholar] [CrossRef]
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