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Article

Polycyclic Aromatic Hydrocarbons (PAHs) Associated with PM2.5 in Guadalajara, Mexico: Environmental Levels, Health Risks and Possible Sources

1
CONACYT, Centro de Investigaciones Químicas-IICBA, Universidad Autónoma del Estado de Morelos, Av. Universidad 1001, Col. Chamilpa, C.P. 62209 Cuernavaca, Mexico
2
Centro de Investigación y Asistencia en Tecnología y Diseño del Estado de Jalisco, Av. Normalistas 800, Col. Colinas de la Normal, C.P. 44270 Guadalajara, Mexico
3
Centro de Investigaciones Químicas-IICBA, Universidad Autónoma del Estado de Morelos, Av. Universidad 1001, Col. Chamilpa, C.P. 62209 Cuernavaca, Mexico
*
Author to whom correspondence should be addressed.
Environments 2018, 5(5), 62; https://doi.org/10.3390/environments5050062
Received: 26 April 2018 / Revised: 16 May 2018 / Accepted: 18 May 2018 / Published: 19 May 2018
(This article belongs to the Special Issue Analysis of Environmental Pollutants)

Abstract

PM2.5 samples were collected from January 2009 to January 2010 at two sampling sites located in the downtown (Centro) and toward the southwest (Miravalle) in the city of Guadalajara, Mexico. The environmental concentrations of 14 selected polycyclic aromatic hydrocarbons (PAHs) in PM2.5 were identified and quantified. The most abundant PAHs in PM2.5 samples were benzo[ghi]perylene, indeno[1,2,3-cd]pyrene, benzo[b]fluoranthene, benzo[a]pyrene and benzo[k]fluoranthene, accounting for approximately 75% of the total PAHs. The total PAH concentrations at the two sampling sites ranged from 0.65 to 19.62 ng·m−3. Spatial variations were found during the dry-warm season, which were attributed mainly to differing intensities of local traffic and less dispersion of air pollutants in Miravalle. Seasonal variations were associated with increases in rainfall (June-September) and differences in temperature (January–May and October–January). The benzo(a)pyrene-equivalent (BaPE) and BaP results suggest that exposure to PM2.5-containing carcinogenic PAHs (C-PAHs) in Miravalle during the warm-dry and cold-dry seasons can be seen as representing a serious risk to human health. The contributions from potential sources to PAHs in PM2.5 were evaluated by the diagnostic ratios between PAHs and principal component analysis (PCA). In the whole sampling period, vehicular emission activity, probably related to light and heavy traffic, was found to be the predominant contributor to PM2.5-bound PAHs.
Keywords: PM2.5; PAHs; source emission; health risks; BaPE PM2.5; PAHs; source emission; health risks; BaPE

1. Introduction

Airborne particulate matter is an atmospheric contaminant that constitutes a potential hazard to citizens in polluted urban areas. Several epidemiological studies [1,2] have enlightened knowledge on this topic. Exposure to the breathable fraction of particulate matter is the most concerning because it has been found that it is the most detrimental to human health [3]. Thus far, particles with a size smaller than 2.5 μm (PM2.5) have shown the most significant association with increases in mortality by lung cancer and cardio-respiratory diseases by long-term exposure [4]. Although there is still disagreement on the main mechanisms responsible for the health effects [5], it is well known that various harmful organic components, elements and inorganic chemical substances, which are all part of particulates, can be a human health risk [6,7].
In the organic fraction of PM2.5, the polycyclic aromatic hydrocarbons (PAHs) are one of the most widely studied groups of organic compounds, since 16 PAHs have been listed as priority pollutants by the U.S. Environmental Protection Agency [8] because they are considered as possible or probable human carcinogens [9,10]. They are also mutagenic and can undergo atmospheric photochemical reaction in the gas phase and on particle surfaces [11,12] and can be photo-chemically transformed into highly toxic compounds such as nitrated (nitro-PAHs) and oxygenated PAHs (oxy-PAHs). They can be emitted from the incomplete combustion of carbon-containing materials and are mostly from anthropogenic sources in urban environments such as coal combustion and vehicular emissions [13]. Furthermore, they are predominantly associated with particles of smaller sizes [14]. Therefore, in order to better understand the air quality and provide more reliable support, it is essential to investigate PAHs associated with breathable particles and their emissions sources in urban zones, which would be used by local government and environmental policymakers to protect human health and improve the well-being of the population.
The Metropolitan Zone of Guadalajara is the second most densely populated area in Mexico. Deterioration of air quality, mainly in dry seasons, may be a consequence of the rapid industrial growth and high vehicular traffic in this area; it was also suggested that atmospheric conditions might favour photochemical oxidants and the blockage of pollutants [15]. Although there is an atmospheric monitoring network and studies on trace metals and inorganic ions in PM2.5 [15,16], it is still necessary to undertake organic chemical characterization of breathable particulate matter to identify sources and to provide support to local government in the design of viable strategies with benefits to the population. A recent study found that naphthalene, phenanthrene, anthracene and chrysene likely undergo photochemical transformation to their quinones compounds, which were found in PM2.5 at three urban locations within the Metropolitan Zone of Guadalajara during the dry and rainy season in 2012 [17]. However, there are no published data on PAHs associated with PM2.5 before 2012. Therefore, this is the first report that focuses on analysis of PAHs in PM2.5 in Guadalajara.
Hence, the aims of this work were to determine the PAH concentrations in PM2.5, evaluate the potential cancer risk and identify the possible sources at two sites and during three seasons in Guadalajara city, México.

2. Materials and Methods

2.1. Material and Reagents

Standards of PAHs were obtained as a mixture, containing naphthalene (Nap), acenaphthylene (Acy), acenaphthene (Acn), fluorene (Flu), phenanthrene (Phe), anthracene (Ant), fluoranthene (Flt), pyrene (Pyr), benzo[a]anthracene (BaA), chrysene (Chry), benzo[b]fluoranthene (BbF), benzo[k]fluoranthene (BkF), benzo[a]pyrene (BaP), indeno[1,2,3-cd]pyrene (IcdP), and benzo[ghi]perylene (BghiP) and dibenz[ah]anthracene (DBahA). Internal standards were also obtained as mixtures consisting of five deuterated PAHs (naphthalene-d8, acenaphthene-d10, Phenanthrene-d10, chrysene-d12, perylene-d12). Both sets of standards were supplied by Restek (Bellefonte, PA, USA). Solvents, HPLC grade, such as methylene chloride, acetone and n-hexane, were purchased from Burdick and Jackson-Honeywell (Muskegon, MI, USA).

2.2. Sampling of PM2.5 and Meteorological Conditions

The study was performed on the flat roofs of two local health facilities at Guadalajara, Jalisco, Mexico. Centro (CEN), situated in the downtown, is an urban site with commercial and service activities and is surrounded by heavily travelled and paved curbed surface streets with light duty vehicles and heavy-duty diesel buses. Miravalle (MIR), located to the southwest in the city of Guadalajara, is 100 m from a major arterial street with fast vehicular traffic and a rapid transport system for passengers and is surrounded by dense residential areas and some industrial facilities (Figure 1). Those places were selected because they have atmospheric monitoring stations run by the Jalisco State Government and have validated historical registers of PM2.5 and meteorological measurements, which were kindly supplied for this study.
The samples of PM2.5 were collected with a Partisol 2300 sampler (Rupprecht & Patashnick Co., Albany, NY, USA) at flow rate of 16.7 L·min−1 on quartz fiber filters (47 mm; Whatman) that were baked (600 °C, 8 h) before the collection to diminish organic compounds adsorbed during their transport and handling. The samples were collected approximately every third day for 24 h from January 2009 to January 2010, transported in a sealed Petri dish and stored until analysis at 4 °C. In order to obtain a sufficient amount of sample to reach the detection threshold of the chemical analysis, a pair of samples was simultaneously collected each day within 24 h, and then both filters were extracted together.
The samples were collected under three different meteorological conditions (Tables S1 and S2): The warm-dry season (WDS), from January through May 2009, was characterized by thermal inversions and the highest temperature (24 ± 2 °C); the rainy season (RS) from June through September 2009 was characterized by higher rainfall and the highest relative humidity (67 ± 17%); and the cold-dry season (CDS), from October (2009) to through January (2010), was characterized by the lowest temperature (20 ± 2°C).

2.3. Determination of PAHs: Analysis and Quality Controls

The HAPs were extracted from PM2.5 twice with 30 mL of methylene chloride at 40 °C by ultrasonic bath (Bransonic) for 30 min. The extraction was carried out in a flask that was fitted to a condenser to avoid volatilization of compounds [18]. The organic extract was concentrated almost to dryness in a rotary evaporator RV10 (IKA), then passed through a Teflon filter (0.44 μm) and adjusted to 0.2 mL. The concentrated extract was then analyzed by gas chromatography (GC) 6890N (Agilent Technologies, Santa Clara, CA, USA) and mass spectrometry (MS) 5975 (Agilent Technologies). The standards of calibration and sample solutions were injected (2 μl) automatically at 280 °C and separated with a capillary column (HP5MS 30 m × 25 mm) with a film thickness of 25 μm (Agilent Technologies) with ultra-high purity (INFRA) helium as the carrier gas at a flow rate of 1 ml·min−1 and by a temperature program that was started at 40 °C, elevated at 20 °C·min−1 to 110 °C, then at 20 °C·min−1 to 300 °C and finally increased at 20 °C·min−1 to 310 °C (maintained for 10 min). The mass spectra were obtained by electronic impact (70 EV) and a quadrupole mass analyzer. The SCAN mode was used to obtain the retention time and to select the m/z that was characteristic of each compound. The quantitation was carried out in SIM mode by calibration curves prepared by dilution of standards, ranging from 1.0–1000 ng/mL, with correlation coefficients (r2) greater than 0.99 and detection limits between 0.83 and 23.50 ng/mL. The environmental concentrations in samples were corrected with blanks and recoveries (58–60%) with CV < 30%; the latter obtained by a previous optimized extraction procedure based on spiked real samples of PM2.5 [19].

2.4. Statistical Analysis

The Mann-Whitney Utest was use to compared medians between sites and seasons. Spearman’s rank test was used to obtain associations among particles, PAHs and meteorological parameters. These tests were applied only when at least three records were obtained and validated. Principal component analysis (PCA) was applied to evaluate emission sources for the whole period for each site.

3. Results and Discussion

3.1. PAHs Concentrations

The average atmospheric concentration ± standard deviation of the sum of 14 PAHs determined in PM2.5 at Guadalajara was 5.65 ± 4.60 ng·m−3 and ranged from 4.55 ± 3.29 ng·m−3 to 10.2 ± ng·m−3 (Tables S1 and S2). The most abundant PAHs were those with higher molecular weight (HMW-PAHs: BghiP, IcdP, BbF, BaP and BkF), accounting for 74.7%, followed by middle molecular weight PAHs (MMW-PAHs: Chry, BaA, Pyr and Flt), accounting for 19.7%, and lower molecular weight PAHs (LMW-PAHs: Phe, Flu, Acy, Acn and Ant), accounting for 5.6% (Figure 2). Because HMW-PAHs have the lowest vapor pressure, that group of compounds tends to be more strongly associated with the particle phase than MMW- and LMW-PAHS [20].
Individual average environmental levels of PAHs in PM2.5 determined in this study ranged from 0.03 ng·m−3 (Acn) to 1.45 ng·m−3 (BghiP), which are the same order of magnitude as those recently reported [17], who found environmental levels of PAHs in PM2.5 ranging from 0.01 ng·m−3 (Flu) to 1.25 ng·m−3 (BghiP) at three urban sites located in Guadalajara, México in 2012. In comparison with Mexico City, the highest city in Mexico, the concentrations found here are of the same order of magnitude as those levels reported by [21] and [22] for five local urban sites, which were found to range from 0.02 ng·m−3 (Flu) to 1.45 ng·m−3 (BghiP) but were approximately one order of magnitude lower than those recently reported, from 0.81 ng·m−3 (Acn) to 2.14 ng·m−3 (BghiP), at an urban and a semi-urban site in Cuernavaca, Mexico [23]. Guadalajara showed similar levels to Latin-American urban areas such as those found in São Paulo, Brazil [24] but much lower levels than those measured in two of Chile’s urban areas, Santiago and Temuco [25]. In USA’s urban sites, the compounds measured were less abundant in cities like Atlanta [26] and those in southern California [27]. Regarding European cities, PAH levels were very similar to suburban and urban areas in Zaragoza, Spain [28], Rome, Italy [29] and in Porto, Portugal [30]. Comparable ambient levels were also reported in Nanjing [31], but the most developed and industrialized Chinese cities presented significantly higher concentrations of those compounds [32,33,34].

3.2. Spatial and Seasonal Patterns

Overall, average atmospheric concentrations of total PAHs were similar between both sites but showed seasonal variation, with the highest environmental levels during the dry seasons and the lowest in the rainy season (Figure 3), similar to a report from Mexico City [22]. Increases in PAH atmospheric concentrations during the cold-dry season may be attributed to lower environmental temperatures, resulting in a stronger tendency of PAH to bond to particles. Also, lower photochemical activity can lead to fewer atmospheric chemical reactions and higher ambient PAH levels, whereas a decrease in the concentrations of these compounds over the rainy season may be mainly attributed to wet deposition. Seasonal trends in Centro are consistent with those atmospheric parameters; the highest levels were found during the coldest season and the lowest were in accordance with rainfall increases and the highest temperatures. Unlike Centro, the median during the dry-warm season for Miravalle was found to be significantly higher (p < 0.05) than that in the cold-dry season (Figure 3b). It was observed that concentrations of HMW PAHs in Miravalle during the dry-warm period were about two times those found in Centro (Figure 3a). Since meteorological conditions such as temperature and relative humidity are similar (Figure 3) at both sites (p > 0.05), the different patterns in Miravalle could be mainly attributed to a substantial contribution of vehicular activity to PM2.5 by local traffic due to the major PAHs in HMW such as IcdP and BghiP, which are indicators of fossil fuel combustion. In comparison with Centro (3.38 m/s), the lower wind speed (2.57 m/s) recorded for Miravalle could favor less dispersion of air pollutants in the warm-dry season.

3.3. Health Risks

In order to assess the carcinogenic potency for humans, the benzo(a)pyrene-equivalent (BaPE) carcinogenicity was calculated by multiplying the concentrations of each PAH species with their corresponding toxic equivalent factors (TEF); thus, atmospheric concentration of Acn, Phe, Pyr, Flt were each multiplied by 0.001, while Ant, Chry and BghiP by 0.01, BaA, BbF, BkF and IcdP by 0.1 and BaP by 1 [13,35]. The mean of the summed BaPE for the whole sampling period was 0.79 ± 0.72 ng·m−3 and ranged between 0.01 ng·m−3 and 2.52 ng·m−3. The values found in Guadalajara were approximately one order of magnitude lower than those recently reported (4.05 ng·m−3) in Cuernavaca, Mexico [23]. Similar levels were found in Florence, Italy (0.34–0.79 ng·m−3) [36], Hamilton, Canada (0.84 ng·m−3) [37] and Nanjing, China (0.42–1.35 ng·m−3) [31], while higher levels were obtained in Xi’an (2–64 ng·m−3) and Guangzhou (0.96–22.46 ng·m−3), China [38,39]. Among those 14 HAPs, five carcinogenic compounds (C-HAPs), including BaA, BbF, BkF, BaP, and IcdP, accounted for more than 50%. In accordance with IARC [9,10] and EPA [8], exposure to C-PAHs can be a considerable risk factor for human health. Although BaP was not the most abundant carcinogenic compound [40], it had the highest relative contribution to total potential carcinogenicity, accounting for 75%. In addition, both BaPE and BaP displayed strong seasonal variation, with their values being higher in the warm and cold seasons than in the rainy season, while they had light spatial variation with higher values in Miravalle than those found in Centro. Therefore, exposure to PM2.5 containing C-PAHs in Miravalle during warm-dry and cold-dry seasons might present a serious risk to human health.

3.4. Sources of PAHs

3.4.1. Overall Identification

It has been shown by several ambient studies of urban districts, suburban sites and rural sites around the world that profile and individual PAHs can be used as tracers to distinguish among their diverse sources [13,24,27,29,41,42,43]. They have been associated with several kinds of sources like biomass burning [26], coal combustion [44], coal processing industries [45] and vehicle emissions [27,46]. In this work, the ratio of LMW, MMW and HMW was approximately 1.0:3.1:12.5 in Centro and 1.0:4.0:14 in Miravalle, indicating the dominance of HMW. It has been reported that higher high molecular weight PAH concentrations mean more typical pyrogenic products derived mainly from fossil fuel combustion [31,47], while light molecular weight-PAHs are related to non-combusted petroleum products [48]. In the urban atmosphere, those HMW-PAHs like BghiP, IcdP and BkF can be considered as tracers for vehicular emissions. In fact, BghiP is regarded as a marker of gasoline vehicles [49], while BghiP, IcdP and BbF are often the most abundant in urban areas where vehicular emission is the main source of PAH [50]. In addition, it has been observed that BghiP, IcdP, BbF, BaA and Chry are linked with both gasoline and diesel emissions [46,51,52]. Therefore, the highest environmental levels of PAHs related to fuel combustion and the influence of intense vehicular traffic in both sites suggested that PAHs in Centro and Miravalle sites may be essentially attributed to traffic exhaust.

3.4.2. Evaluation of Diagnostic Ratios

PAH isomer pair ratios are frequently used to identify the possible sources for PAHs in ambient air. The IcdP/(IcdP + BghiP), BaA/(BaA + Chry), Flt/(Flt + Pyr) and Ant/(Ant + Phe) ratios were used due to their relative stability (Figure 4). In this study, the calculated ratio values suggested a substantial contribution from vehicular traffic emissions to PM2.5 within the Centro and Miravalle sampling areas. The ratios of IcdP/(IcdP + BghiP) varied between 0.30 and 0.52 (0.40 ± 0.05) for Centro and between 0.22 and 0.53 (0.42 ± 0.09) for Miravalle. Those values were in accordance with the range 0.20 to 0.50, where in previous studies it was shown that, for these values, the PAHs originate from petroleum sources such as liquid fossil fuel, vehicle and oil combustion [53], and those between 0.35 and 0.70 imply diesel emissions [54]. The BaA/(BaA + Chry) ratios obtained, 0.40–0.52 (0.47 ± 0.04) for Centro and 0.35–0.56 (0.44 ± 0.05) for Miravalle, were similar to 0.38–0.64 and 0.22–0.55, which have been associated with diesel and gasoline emissions, respectively [55,56]. The values of Flt/(Flt + Pyr) were 0.22–0.50 (0.45 ± 0.07) for Centro and 0.16–0.56 (0.45 ± 0.08) for Miravalle. These values are close to 0.4-0.5, which were attributed to the contribution of liquid fossil fuel combustion [57,58], specifically from gasoline combustion emissions [59]. The ratios of Ant/(Ant + Phe) were 0.02-0.20 (0.14 ± 0.05) for Centro and 0.05–0.51 (0.18 ± 0.10) for Miravalle, with most of the values >0.1, suggesting association with combustion sources [60].

3.4.3. Principal Component Analysis (PCA)

In addition to diagnostic ratios, PCA was conducted on each data set and site showing that the main contributors to PAHs were vehicular emissions activity, probably related to light and heavy traffic. However, other sources were also found, such as biomass burning and wood combustion and to a lesser extent coal combustion. For Centro (Table 1), PC1 was highly loaded with high (BbF, IcdP, BghiP) and middle (BaA, Chry) molecular weight PAHs. IcdP is one of the tracers for gasoline vehicles [61]. BbF is used as one of the indicators for heavy-duty diesel vehicles emissions [62]. BghiP, BbF, BaA and Chry are markers of gasoline and diesel vehicles [46,50,63]. This finding is similar to those sources suggested by diagnostic ratio analysis, which also showed that fossil fuel combustion contributed to PM2.5 in Centro. This is consistent with characteristics of vehicular traffic in Centro; this site is heavily traveled by light-duty vehicles and heavy-duty diesel buses. PC2 was predominately loaded with light molecular weight PAHs (Acn, Flu), showing an association with biomass burning or coal combustion [64]. PC3 included Phe (3-rings) and Pyr (4-rings) which are frequently associated with either wood [24] or coal combustion [65]. For Miravalle (Table 2), PC1 was highly loaded with Flt, BaA, Chry, BbF, BkF, BaP, IcdP and BghiP, which are primarily associated with gasoline and diesel vehicles [52,66]. The diagnostic ratio analysis in Miravalle was similar to PC1, i.e., PAHs in PM2.5 are a result of mainly diesel and gasoline emissions, which are consistent with fast vehicular traffic and a rapid transport system for passengers on streets near this site. PC2 was loaded with Flu, Phe and Pyr, which are linked to wood combustion [67]. PC3 was loaded with Acn, Flu, and Ant, and PC4 with only Ant, which indicated contributions from biomass burning [68] and coal combustion [50,69], respectively.

4. Conclusions

Fourteen PAHs associated with PM2.5 were identified and quantified at a downtown location (Centro) and an urban sector (Miravalle) located in the Metropolitan Zone of Guadalajara in Mexico. The most abundant PAHs were HMW (BghiP, IcdP, BbF, BaP and BkF) followed by MMW (Chry, BaA, Pyr and Flt) and LMW (Phe, Flu, Acy, Ace and Ant). The atmospheric concentrations of PAHs showed seasonal variation, with high environmental levels during the driest seasons and lowest levels in the rainy season, due mainly to temperature and wet deposition. Spatial variation was only observed during the warm-dry season. The median of total PAHs in Miravalle was found to be the highest significantly (p < 0.05), which was attributed to a substantial contribution by vehicular activity to PM2.5 from local traffic. Benzo[a]pyrene-equivalent (BaPE) carcinogenicity and contribution by BaP showed that exposure to PM2.5 in Miravalle during the warm and cold seasons could represent a serious risk to human health. The PCA and diagnostic ratio showed that contribution from vehicular traffic emissions to PM2.5 was probably the main source of PAHs in PM2.5 collected in Centro and Miravalle.

Supplementary Materials

The following are available online at https://www.mdpi.com/2076-3298/5/5/62/s1. Table S1: PAH atmospheric concentrations (ng·m−3) in PM2.5 and meteorological conditions at the Centro site (2009–2010), Table S2: PAH atmospheric concentrations (ng m−3) in PM2.5 and meteorological conditions at the Miravalle site (2009–2010), Table S3: Concentrations of PAHs in PM2.5 at several sites around world.

Author Contributions

Conceptualization and Writing-Original Draft Preparation, M.A.M.-T.; Formal Analysis, A.B.-G. and M.I.A.-M.; Validation, H.A.S.-N.

Funding

This research received no external funding.

Acknowledgments

The authors wish to thank Secretaria del Medio Ambiente para el Desarrollo Sustentable del Estado de Jalisco (SEMADES) and Consejo Nacional de Ciencia y Tecnología (2121).

Conflicts of Interest

The authors declare no conflict of interest.

References

  1. Englert, N. Fine particles and human health—A review of epidemiological studies. Toxicol. Lett. 2004, 149, 235–242. [Google Scholar] [CrossRef] [PubMed]
  2. Kappos., A.D.; Bruckmann, P.; Eikmann, T.; Englert, N.; Heinrich, U.; Höppe, P.; Koch, E.; Krause, G.H.M.; Kreyling, W.G.; Rauchfuss, K.; et al. Health effects of particles in ambient air. Int. J. Hyg. Environ. Health 2004, 207, 399–407. [Google Scholar] [CrossRef] [PubMed]
  3. Ramgolam, K.; Favez, O.; Cachier, H.; Gaudichet, A.; Marano, F.; Martinon, L.; Baeza-Squiban, A. Size-Partitioning of an urban aerosol to identify particle determinants involved in the proinflammatory response induced in airway epithelial cells. Part. Fibre Toxicol. 2009, 6, 1–12. [Google Scholar] [CrossRef] [PubMed]
  4. Pope, C.A., III; Burnett, R.T.; Thun, M.J.; Calle, E.E.; Krewski, D.; Ito, K.; Thurston, G.D. Lung cancer, cardiopulmonary mortality, and long-term exposure to fine particulate air pollution. JAMA 2002, 287, 1132–1141. [Google Scholar] [CrossRef] [PubMed]
  5. Feng, S.; Gao, D.; Liao, F.; Zhou, F.; Wang, X. The health effects of ambient PM2.5 and potential mechanisms. Ecotoxicol. Environ. Saf. 2016, 128, 67–74. [Google Scholar] [CrossRef] [PubMed]
  6. Gao, Y.; Guo, X.; Ji, H.; Li, C.; Ding, H.; Briki, M.; Tang, L.; Zhang, Y. Potential threat of heavy metals and PAHs in PM2.5 in different urban functional areas of Beijing. Atmos. Res. 2016, 178–179, 6–16. [Google Scholar] [CrossRef]
  7. Villalobos-Pietrini, R.; Hernández-Mena, L.; Amador-Muñoz, O.; Munive-Colín, Z.; Bravo-Cabrera, J.L.; Gómez-Arroyo, S.; Frías-Villegas, A.; Waliszewski, S.; Ramírez-Pulido, J.; Ortiz-Muñiz, R. Biodirected mutagenic chemical assay of PM10 extractable organic matter in Southwest Mexico City. Mutat. Res. 2007, 634, 192–204. [Google Scholar] [CrossRef] [PubMed]
  8. U.S. Environmental Protection Agency (EPA). Integrated Risk Information System (IRIS); EPA: Duluth, MN, USA, 1994.
  9. International Agency of Research on Cancer (IARC). Agents Reviewed by the IARC Monographs, Volume 1–95, 2007. Available online: http://monographs.iarc.fr/ENG/Monographs/vol92/index.php (assessed on 26 April 2018).
  10. International Agency of Research on Cancer (IARC). Overall Evaluation of Carcinogenicity: An Updating of IARC Monographs Volumes 1 to 42; IARC: Lyon, France, 1987. [Google Scholar]
  11. Cochran, R.E.; Jeong, H.; Haddadi, S.; Fisseha-Derseh, R.; Gowan, A.; Beránek, J.; Kubátová, A. Identification of products formed during the heterogeneous nitration and ozonation of polycyclic aromatic hydrocarbons. Atmos. Environ. 2016, 128, 92–103. [Google Scholar] [CrossRef]
  12. Walgraeve, C.; Demeestere, K.; Dewulf, J.; Zimmermann, R.; Van Langenhove, H. Oxygenated polycyclic aromatic hydrocarbons in atmospheric particulate matter: Molecular characterization and occurrence. Atmos. Environ. 2010, 44, 1831–1846. [Google Scholar] [CrossRef]
  13. Akyüz, M.; Çabuk, H. Particle-associated polycyclic aromatic hydrocarbons in the atmospheric environment of Zonguldak, Turkey. Sci. Total Environ. 2008, 405, 62–70. [Google Scholar] [CrossRef] [PubMed]
  14. Slezakova, K.; Castro, D.; Delerue-Matos, C.; Alvim-Ferraz, M.; Morais, S.; Pereira, M. Impact of vehicular traffic emissions on particulate-bound PAHs: Levels and associated health risks. Atmos. Res. 2013, 127, 141–147. [Google Scholar] [CrossRef]
  15. Murillo-Tovar, M.A.; Saldarriaga-Noreña, H.; Hernández-Mena, L.; Campos-Ramos, A.; Cárdenas-González, B.; Ospina-Noreña, J.E.; Cosío-Ramírez, R.; Díaz-Torres, J.J.; Smith, W. Potential Sources of Trace Metals and Ionic Species in PM2.5 in Guadalajara, México: A case Study during Dry Season. Atmosphere 2015, 6, 1858–1870. [Google Scholar] [CrossRef]
  16. Saldarriaga-Noreña, H.; Waliszewski, S.; Murillo-Tovar, M.; Hernández-Mena, L.; De la Garza-Rodríguez, I.; Colunga-Urbina, E.; Cuevas-Ordaz, R. Acid Gases and Nitrate and Sulfate Particles in the Atmosphere in the City of Guadalajara, México. Bull. Environ. Contam. Toxicol. 2012, 88, 730–734. [Google Scholar] [CrossRef] [PubMed]
  17. Barradas-Gimate, A.; Murillo-Tovar, M.A.; Díaz-Torres, J.J.; Hernández-Mena, L.; Saldarriaga-Noreña, H.; Delgado-Saborit, J.M.; López-López, A. Occurrence and Potential Sources of Quinones Associated with PM2.5 in Guadalajara, Mexico. Atmosphere 2017, 8, 140. [Google Scholar] [CrossRef]
  18. Valle-Hernández, B.L.; Mugica-Álvarez, V.; Salinas-Talavera, E.; Amador-Muñoz, M.A.; Villalobos-Pietrini, R.; De Vizcaya-Ruíz, A. Temporal variation of nitro-polycyclic Aromatic hydrocarbons in PM10 and PM2.5 collected in Northern Mexico City. Sci. Total Environ. 2010, 408, 5429–5438. [Google Scholar] [CrossRef] [PubMed]
  19. Flores-Arriola, A.; Murillo-Tovar, M.A.; Saldarriaga-Noreña, H.A.; Hernández-Mena, L.; Amador-Muñoz, O. Hidrocarburos aromáticos policíclicos asociados con partículas respirables finas en el Área Metropolitana de Guadalajara, México: un caso de estudio sobre la presencia, riesgos a la salud y potenciales fuentes. In Proceedings of the XXVIII Congreso Nacional de Química Analítica, Guerrero, México, 24–27 June 2015; pp. 263–269. [Google Scholar]
  20. Albinet, A.; Leoz-Garziandia, E.; Budzinski, H.; Villenave, E.; Jaffrezo, J.-L. Nitrated and oxygenated derivatives of polycyclic aromatic hydrocarbons in the ambient air of two French alpine valleys Part 1: Concentrations, sources and gas/particle partitioning. Atmos. Environ. 2008, 42, 43–54. [Google Scholar] [CrossRef][Green Version]
  21. Murillo-Tovar, M.A. Optimización de las Condiciones Analíticas Para la Determinación Simultánea de n-Alcanos, Hidrocarburos Aromáticos Policíclicos y sus Derivados Oxigenados en las Aeropartículas ≤ 2.5 µm. Ph.D. Thesis, Universidad Nacional Autónoma de México, Ciudad de México, México, 30 August 2012. [Google Scholar]
  22. Amador-Muñoz, O.; Villalobos-Pietrini, R.; Miranda, J.; Vera-Avila, L.E. Organic compounds of PM2.5 in Mexico Valley: Spatial and temporal patterns, behavior and Sources. Sci. Total Environ. 2011, 409, 1453–1465. [Google Scholar] [CrossRef] [PubMed]
  23. Saldarriaga-Noreña, H.; López-Márquez, R.; Murillo-Tovar, M.; Hernández-Mena, L.; Ospina-Noreña, E.; Sánchez-Salinas, E.; Waliszewski, S.; Montiel-Palma, S. Analysis of PAHs Associated with Particulate Matter PM2.5 in Two Places at the City of Cuernavaca, Morelos, México. Atmosphere 2015, 6, 1259–1270. [Google Scholar] [CrossRef]
  24. Bourotte, C.; Fortic, M.C.; Taniguchi, S.; Bícego, M.C.; Lotufo, P.A. A wintertime study of PAHs in fine and coarse aerosols in Sao Paulo City, Brazil. Atmos. Environ. 2005, 39, 3799–3811. [Google Scholar] [CrossRef]
  25. Tsapakis, M.; Lagoudaki, E.; Stephanou, E.G.; Kavouras, I.G.; Koutrakis, P.; Oyola, P.; Baer, D. The composition and sources of PM2.5 organic aerosol in two urban areas of Chile. Atmos. Environ. 2002, 36, 3851–3863. [Google Scholar] [CrossRef]
  26. Li, Z.; Porter, E.N.; Sjödin, A.; Needham, L.L.; Lee, S.; Rusell, A.G.; Mulholland, J.A. Characterization of PM2.5-bound polycyclic aromatic hydrocarbons in Atlanta—Seasonal variations at urban, suburban, and rural ambient air monitoring sites. Atmos. Res. 2009, 43, 4187–4193. [Google Scholar] [CrossRef]
  27. Eiguren-Fernandez, A.; Miguel, A.H.; Froines, J.R.; Thurairatnam, S.; Avol, E.L. Seasonal and spatial variation of polycyclic aromatic hydrocarbons in vapor-phase and PM2.5 in southern California urban and rural communities. Aerosol Sci. Technol. 2004, 38, 447–455. [Google Scholar] [CrossRef]
  28. Callén, M.S.; Iturmendi, A.; López, J.M. Source apportionment of atmospheric PM2.5-bound polycyclic aromatic hydrocarbons by a PMF receptor model. Assessment of potential risk for human health. Environ. Pollut. 2014, 195, 167–177. [Google Scholar] [CrossRef] [PubMed]
  29. Finardi, S.; Radice, P.; Cecinato, A.; Gariazzo, C.; Gherardi, M.; Romagnoli, P. Seasonal variation of PAHs concentration and source attributtion through diagnostic ratios analysis. Urban Clim. 2017, 22, 19–34. [Google Scholar] [CrossRef]
  30. Albuquerque, M.; Coutinho, M.; Borrego, C. Long-term monitoring and seasonal analysis of polyciclic Aromatic hydrocarbons (PAHs) measured over a decade in the ambient air of Porto, Portugal. Sci. Total Environ. 2016, 543, 439–448. [Google Scholar] [CrossRef] [PubMed]
  31. Li, X.; Kong, S.; Yin, Y.; Li, L.; Yuan, L.; Li, Q.; Xiao, H.; Chen, K. Polycyclic aromatic hydrocarbons (PAHs) in atmospheric PM2.5 around 2013 Asian Youth Games period in Nanjing. Atmos. Res. 2016, 174–175, 85–86. [Google Scholar] [CrossRef]
  32. Musa-Bandowe, B.A.; Meusel, H.; Huang, R.J.; Ho, K.; Cao, J.; Hoffmann, T.; Wilcke, W. PM2.5-bound oxygenated PAHs, nitro-PAHs and parent-PAHs from the atmosphere of Chinese megacity: Seasonal variation, sources and cancer risk assessment. Sci. Total Environ. 2014, 473–474, 77–87. [Google Scholar] [CrossRef] [PubMed]
  33. Wang, J.; Li, X.; Jiang, N.; Zhang, W.; Zhang, R.; Tang, X. Long term observations of PM2.5-associated PAHs: Comparisons between normal and episode days. Atmos. Environ. 2015, 104, 228–236. [Google Scholar] [CrossRef]
  34. Wu, D.; Wang, Z.; Chen, J.; Kong, S.; Fu, X.; Deng, H.; Shao, G.; Wu, G. Polycyclic aromatic hydrocarbons (PAHs) in atmospheric PM2.5 and PM10 at a coal-based industrial city: Implication for PAH control at industrial agglomeration regions, China. Atmos. Res. 2014, 149, 217–229. [Google Scholar] [CrossRef]
  35. Di Vaio, P.; Cocozziello, B.; Corvino, A.; Florino, F.; Frecentrese, F.; Magli, E.; Onorati, G.; Saccone, I.; Santagada, V.; Settimo, G.; et al. Level, potential sources of polycyclic aromatic hydrocarbons (PAHs) in particulate matter (PM10) in Naples. Atmos. Environ. 2016, 129, 186–196. [Google Scholar] [CrossRef]
  36. Martellini, T.; Giannoni, M.; Lepri, L.; Katsoyiannis, A.; Cincinelli, A. One year intensive PM2.5-bound polycyclic aromatic hydrocarbons monitoring in the area of Tuscany, Italy. Concentrations, source understanding and implications. Environ. Pollut. 2012, 164, 252–258. [Google Scholar] [CrossRef] [PubMed]
  37. Anastasopoulos, A.T.; Wheeler, A.J.; Karman, D.; Kulka, R.H. Intraurban concentrations, spatial variability and correlation of ambient polycyclic aromatic hydrocarbons (PAH) and PM2.5. Atmos. Environ. 2012, 59, 272–283. [Google Scholar] [CrossRef]
  38. Jia, Y.; Stone, D.; Wang, W.; Schrlau, J.; Tao, S.; Simonich, S.L.M. Estimated reduction in cancer risk due to PAH exposures if source control measures during the 2008 Beijing Olympics were sustained. Environ. Health Perspect. 2011, 119, 815–820. [Google Scholar] [CrossRef] [PubMed]
  39. Liu, J.; Man, R.; Ma, S.; Li, J.; Wu, Q.; Peng, J. Atmospheric levels and health risk of polycyclic aromatic hydrocarbons (PAHs) bound to PM2.5 in Guangzhou, China. Mar. Pollut. Bull. 2015, 100, 134–143. [Google Scholar] [CrossRef] [PubMed]
  40. He, J.; Fan, S.; Meng, Q.; Sun, Y.; Zhang, J.; Fu, F. Polycyclic aromatic hydrocarbons (PAHs) associated with fine particle matters in Nanjing, China: Distributions, sources and meteorological influences. Atmos. Environ. 2014, 89, 207–215. [Google Scholar] [CrossRef]
  41. Baek, S.O.; Field, R.A.; Goldstone, M.E.; Kirk, P.W.; Lester, J.N.; Perry, R. A review of atmospheric polycyclic aromatic hydrocarbons: Sources, fate and behavior. Water Air Soil Pollut. 1991, 60, 279–300. [Google Scholar] [CrossRef]
  42. Kong, S.; Li, X.; Li, L.; Yin, Y.; Chen, K.; Yuan, L.; Zhang, Y.; Shan, Y.; Ji, Y. Variation of polycyclic aromatic hydrocarbons in atmospheric PM2.5 during winter haze period around 2014 Chinese Spring Festival at Nanjing: Insights of source changes, air mass direction and firework particle injection. Sci. Total Environ. 2015, 520, 59–72. [Google Scholar] [CrossRef] [PubMed]
  43. Kulkarni, P.; Venkataraman, C. Atmospheric polycyclic aromatic hydrocarbons in Mumbai, India. Atmos. Environ. 2000, 34, 2785–2790. [Google Scholar] [CrossRef]
  44. Kanan, K.; Johnson-Restrepo, B.; Yohn, S.S.; Giesy, J.P.; Long, D.T. Spatial and temporal distribution of polycyclic aromatic hydrocarbons in sediments from Michigan Inland Lakes. Environ. Sci. Technol. 2005, 39, 4700–4706. [Google Scholar] [CrossRef]
  45. Guo, H.; Lee, S.C.; Ho, K.F.; Wang, X.M.; Zou, S.C. Particle-associated polycyclic aromatic hydrocarbons in urban air of Hong Kong. Atmos. Environ. 2003, 37, 5307–5317. [Google Scholar] [CrossRef]
  46. Chen, F.; Hu, W.; Zhong, Q. Emissions of particle-phase polycyclic aromatic hydrocarbons (PAHs) in the Fu Gui-shan Tunnel of Nanjing, China. Atmos. Res. 2013, 124, 53–60. [Google Scholar] [CrossRef]
  47. Zhou, J.B.; Wang, T.G.; Huang, Y.B.; Mao, T.; Zhong, N.N. Size distribution of polycyclic aromatic hydrocarbons in urban and suburban sites of Beijing, China. Chemosphere 2006, 61, 792–799. [Google Scholar] [CrossRef] [PubMed]
  48. Hassanien, M.A.; Abdel-Latif, N.M. Polycyclic aromatic hydrocarbons in road dust over Greater Cairo, Egypt. J. Hazard. Mater. 2008, 151, 247–254. [Google Scholar] [CrossRef] [PubMed]
  49. Kong, S.F.; Ding, X.; Bai, Z.P.; Han, B.; Chen, L.; Shi, J.W.; Li, Z.Y. A seasonal study of polycyclic aromatic hydrocarbons (PAHs) in fine and coarse atmospheric particulate matter in five typical cities of Liaoning Province, China. J. Hazard. Mater. 2010, 183, 70–80. [Google Scholar] [CrossRef] [PubMed]
  50. Wu, Y.; Yang, L.; Zheng, X.; Zhang, S.; Song, S.; Li, J.; Hao, J. Characterization and source apportionment of particulate PAHs in the roadside environment in Beijing. Sci. Total Environ. 2014, 470–471, 76–83. [Google Scholar] [CrossRef] [PubMed]
  51. Ho, K.F.; Ho, S.S.H.; Lee, S.C.; Cheng, Y.; Chow, J.C.; Watson, J.G.; Louie, P.K.K.; Tian, L. Emissions of gas- and particle-phase polycyclic aromatic hydrocarbons (PAHs) in the Shing Mun Tunnel, Hong Kong. Atmos. Environ. 2009, 43, 6343–6351. [Google Scholar] [CrossRef]
  52. Fang, G.; Chang, C.; Wu, Y.; Fu, P.; Yang, L.; Chen, M. Characterization, identification of ambient air and road dust polycyclic aromatic hydrocarbons in Central Taiwan Taichung. Sci. Total Environ. 2004, 327, 135–146. [Google Scholar] [CrossRef] [PubMed]
  53. 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]
  54. Kavouras, I.G.; Koutrakis, P.; Tsapakis, M.; Lagoudaki, E.; Stephanou, E.G.; Von Baer, D.; 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] [PubMed]
  55. Manoli, E.; Kouras, A.; Samara, C. Profile analysis of ambient and source emitted particle-bound polycyclic aromatic hydrocarbons from three sites in northern Greece. Chemosphere 2004, 56, 867–878. [Google Scholar] [CrossRef] [PubMed]
  56. Shi, G.; Liu, G.; Tian, Y.; Zhou, X.; Peng, X.; Feng, Y. Chemical characteristic and toxicity assessment of particle associated PAHs for the short-term anthropogenic activity event: During the Chinese New Year’s Festival in 2013. Sci. Total Environ. 2014, 482–483, 8–14. [Google Scholar] [CrossRef] [PubMed]
  57. Tan, J.H.; Guo, S.J.; Ma, Y.L.; Duan, J.C.; Cheng, Y.; He, K.B.; Yang, F.M. Characteristics of particulate PAHs during a typical haze episode in Guangzhou, China. Atmos. Res. 2011, 102, 91–98. [Google Scholar] [CrossRef]
  58. Yang, D.; Qi, S.H.; Zhang, Y. Levels, sources and potential risks of polycyclic aromatic hydrocarbons (PAHs) in multimedia environment along the Jinjiang River mainstream to Quanzhou Bay, China. Mar. Pollut. Bull. 2013, 76, 298–306. [Google Scholar] [CrossRef] [PubMed]
  59. Han, B.; Ding, X.; Bai, Z.; Kong, S.; Guo, G. Source analysis of particulate matter associated polycyclic aromatic hydrocarbon (PAHs) in an industrial city in northeastern China. J. Environ. Monit. 2011, 13, 2597–2604. [Google Scholar] [CrossRef] [PubMed]
  60. Jiang, Y.F.; Hua, X.F.; Yves, U.J.; Zhang, H.; Wu, Y. Status, source and health risk assessment of polycyclic aromatic hydrocarbons in street dust of an industrial city, NW China. Ecotoxicol. Environ. Saf. 2014, 106, 11–18. [Google Scholar] [CrossRef] [PubMed]
  61. Ravindra, K.; Bencs, L.; Wauters, E.; Hoog, J.; Deutsch, F.; Roekens, E.; Bleux, N.; Berghmans, P.; Grieken, R. Seasonal and site-specific variation in vapour and aerosol phase PAHs over Flanders (Belgium) and their relation with anthropogenic activities. Atmos. Environ. 2006, 40, 771–785. [Google Scholar] [CrossRef]
  62. Hong, H.S.; Yin, H.L.; Wang, X.H.; Ye, C.X. Seasonal variation of PM10-bound PAHs in the atmosphere of Xiamen, China. Atmos. Res. 2007, 85, 429–441. [Google Scholar] [CrossRef]
  63. Sadiktsis, I.; Bergvall, C.; Johansson, C. Automobile tires—A potential source of highly carcinogenic dibenzopyrenes to the environment. Environ. Sci. Technol. 2012, 46, 3326–3334. [Google Scholar] [CrossRef] [PubMed]
  64. Kong, S.F.; Ji, Y.Q.; Li, Z.Y.; Lu, B.; Bai, Z.P. Emission and profile characteristic of polycyclic aromatic hydrocarbons in PM10 and PM2.5 from stationary sources based on dilution sampling. Atmos. Environ. 2013, 77, 155–165. [Google Scholar] [CrossRef]
  65. Tian, F.L.; Chen, J.W.; Qiao, X.L.; Wang, Z.; Yang, P.; Wang, D.G.; Ge, L.K. Sources and seasonal variation of atmospheric polycyclic aromatic hydrocarbons in Dalian, China: Factor analysis with non-negative constraints combined with local source fingerprints. Atmos. Environ. 2009, 43, 2747–2753. [Google Scholar] [CrossRef]
  66. Ravindra, K.; Sokhi, R.; Grieken, R.V. Atmospheric polycyclic aromatic hydrocarbons: Source attribution, emissions factors and regulation. Atmos. Environ. 2008, 42, 2895–2921. [Google Scholar] [CrossRef][Green Version]
  67. Wang, X.F.; Cheng, H.X.; Xu, X.B.; Zhuang, G.M.; Zhao, C.D. A wintertime study of polycyclic aromatic hydrocarbons in PM2.5 and PM2.5–10 in Beijing: Assessment of energy structure conversion. J. Hazard. Mater. 2008, 157, 47–56. [Google Scholar] [CrossRef] [PubMed]
  68. Larsen, R.K.; Baker, J.E. Source apportionment of polycyclic aromatic hydrocarbons in the urban atmosphere: A comparison of three methods. Environ. Sci. Technol. 2003, 37, 1873–1881. [Google Scholar] [CrossRef] [PubMed]
  69. Sofowote, U.M.; McCarry, B.E.; Marvin, C.H. Source apportionment of PAH in Hamilton Harbour suspended sediments: Comparison of two factor analysis methods. Environ. Sci. Technol. 2008, 42, 6007–6014. [Google Scholar] [CrossRef] [PubMed]
Figure 1. Location of the sampling sites in Guadalajara, Jalisco (Mexico).
Figure 1. Location of the sampling sites in Guadalajara, Jalisco (Mexico).
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Figure 2. Abundance of the polycyclic aromatic hydrocarbons (PAHs) by molecular weight. LMW: lower molecular weight, MMW: middle molecular weight, HMW: higher molecular weight.
Figure 2. Abundance of the polycyclic aromatic hydrocarbons (PAHs) by molecular weight. LMW: lower molecular weight, MMW: middle molecular weight, HMW: higher molecular weight.
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Figure 3. PAH molecular weight distribution over the three seasons in (a) Centro and (b) Miravalle. WDS: warm-dry season, RS: rainy season, CDS: cold-dry season.
Figure 3. PAH molecular weight distribution over the three seasons in (a) Centro and (b) Miravalle. WDS: warm-dry season, RS: rainy season, CDS: cold-dry season.
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Figure 4. PAH cross plots for the ratios of (a) BaA/(BaA + Chry) vs IcdP/(IcdP + BghiP) and (b) Ant/(Ant + Phe) vs Flt/(Flt + Pyr) in Centro and Miravalle.
Figure 4. PAH cross plots for the ratios of (a) BaA/(BaA + Chry) vs IcdP/(IcdP + BghiP) and (b) Ant/(Ant + Phe) vs Flt/(Flt + Pyr) in Centro and Miravalle.
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Table 1. Results of principal component analysis applied to concentrations of 14 Polycyclic Aromatic Hydrocarbons (PAHs) in PM2.5 in Centro.
Table 1. Results of principal component analysis applied to concentrations of 14 Polycyclic Aromatic Hydrocarbons (PAHs) in PM2.5 in Centro.
PAHsPC1PC2PC3
Acy0.47−0.630.41
Acn−0.191.08−0.12
Flu0.280.870.24
Phe0.25−0.030.95
Ant0.86−0.340.23
Flt0.890.030.33
Pyr0.680.000.69
BaA0.96−0.050.24
Chry0.94−0.070.27
BbF0.95−0.070.22
BkF0.900.050.18
BaP0.96−0.130.11
IcdP0.96−0.010.26
BghiP0.890.050.43
Eigenvalue9.882.391.01
Variance cumulative (%)67.8784.2391.15
PC: principal component, meaningful components were shown in bold.
Table 2. Results of principal component analysis applied to concentrations of 14 Polycyclic Aromatic Hydrocarbons (PAHs) in PM2.5 in Miravalle.
Table 2. Results of principal component analysis applied to concentrations of 14 Polycyclic Aromatic Hydrocarbons (PAHs) in PM2.5 in Miravalle.
PAHsPC1PC2PC3PC4
Acy0.290.79−0.24−0.04
Ace0.02−0.13−0.090.99
Flu0.080.460.980.20
Phe−0.130.860.41−0.11
Ant0.05−0.060.88−0.24
Flt0.860.390.23−0.11
Pyr0.470.770.39−0.09
BaA0.960.210.030.05
Chry0.930.270.11−0.08
BbF0.990.070.01−0.00
BkF0.970.020.000.07
BaP0.930.130.020.14
IcdP0.930.03−0.07−0.19
BghiP0.940.000.060.07
Eigenvalue7.922.901.281.13
Variance cumulative (%)54.0373.8082.5690.26
PC: principal component, meaningful components were shown in bold.
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