Next Article in Journal
A Study of Preliminary Breakdown and Return Stroke Processes in High-Intensity Negative Lightning Discharges
Next Article in Special Issue
Inverse Modeling of Nitrogen Oxides Emissions from the 2010 Russian Wildfires by Using Satellite Measurements of Nitrogen Dioxide
Previous Article in Journal
A Review on Predicting Ground PM2.5 Concentration Using Satellite Aerosol Optical Depth
Previous Article in Special Issue
Satellite Assessments of Tropopause Dry Intrusions Correlated to Mid-Latitude Storms
 
 
Search for Articles:
Title / Keyword
Author / Affiliation / Email
Journal
Article Type
 
 
Advanced Search
 
Section
Special Issue
Volume
Issue
Number
Page
 
Journals
Atmosphere
Volume 7
Issue 10
10.3390/atmos7100131
atmosphere-logo
Submit to this Journal Review for this Journal Propose a Special Issue
► Article Menu

Article Menu

share Share announcement Help format_quote Cite question_answer Discuss in SciProfiles thumb_up
...
Endorse textsms
...
Comment
first_page
settings
Order Article Reprints
Font Type:
Arial Georgia Verdana
Font Size:
Aa Aa Aa
Line Spacing:
Column Width:
Background:
Article

Measurements and Analysis of Polycyclic Aromatic Hydrocarbons near a Major Interstate

by
Dennis K. Mikel
* and
Viney P. Aneja
Marine, Earth and Atmospheric Sciences Department, North Carolina State University, Raleigh, NC 27695-8208, USA
*
Author to whom correspondence should be addressed.
Atmosphere 2016, 7(10), 131; https://doi.org/10.3390/atmos7100131
Submission received: 19 August 2016 / Revised: 8 October 2016 / Accepted: 12 October 2016 / Published: 16 October 2016
(This article belongs to the Special Issue Selected Papers from The 1st International Electronic Conference on Atmospheric Sciences)
Browse Figures
Versions Notes

Abstract

:
Polycyclic aromatic hydrocarbons (PAHs) were measured near Interstate 40, just east of Research Triangle Park, North Carolina, USA. The goals of this project were to ascertain whether a sufficient quantity of PAHs could be collected using low flow (16.7 L/minute) over 8-h periods and if so, do investigate how the PAHs correlate to local sources, atmospheric pollutants and meteorology. The 8-h integrated samples were collected on 20 sampling days over a two month period during fall 2014. The samples were collected using low flow (BGI Incorporated PQ200) fine particulate samplers analyzed using gas chromatography-mass spectrometry (GC-MS). Temporal distributions of the PAHs (average mean 9.2 nanogram/cubic meter ±9.0 std) were compared to traffic count, and meteorological and pollutant data collected at the near roadway station. Using the meteorological data (i.e., wind speed and direction vector data), wind roses were created illustrating the local sources of the PAHs. In terms of correlation to atmospheric oxidants, (i.e., ozone, nitrogen dioxide and nitric oxide) wind rose analysis illustrated the morning hours which were predominantly southern winds, while the afternoon hours illustrated southerly and easterly winds, which suggests that the automobile traffic is the main source of PAHs. The nighttime hours wind rose shows winds from the northerly and easterly direction, which are predominantly from the RDU International Airport. Since the wind direction vectors illustrated that the afternoon hours (i.e., 12 p.m. to 8 p.m.) were from the interstate, comparisons were performed on the samples collected in this time period for both the traffic and pollutant data. The comparison of the traffic data showed a correlation with the number of vehicles (>60 feet i.e., heavy duty diesel engine vehicles). In addition, with the ozone, nitrogen dioxide and nitric oxide) there is a significant linear correlation between the sum of the measured PAHs with nitric oxide (NO), nitrogen dioxide (NO2) and ozone (O3) with the R2 values being 0.1, 0.04 and 0.07 respectively. An analysis of variance (ANOVA) statistical regression was performed on the pollutant data versus the measured sum of the PAHs. With the alpha set at 0.05, (α = 0.05) the p-values for O3, NO2 and NO were 0.00613, 0.000496 and 0.000264, respectively, which are significant. In addition, the PAH concentration found in this study compare favorably to other published studies (0.1 to 193.6 ng/m3) both nationally and internationally.

1. Introduction

Polycyclic Aromatic Hydrocarbons (PAHs), which are the byproduct of combustion, exist in the atmosphere in both gas and particulate phases. Naphthalene, which is the simplest PAH, consists of two fused benzene rings. Naphthalene and some of the other lower molecular weight PAHs can exist in the gas phase. However, most PAHs exist in the particulate phase, usually adsorbed onto the surface of fine particulate matter (i.e., particles with an aerodynamic diameter smaller than 2.5 μm).
Epidemiologic research over the last 30 years has shown increases in adverse cardiovascular and respiratory outcomes in relation to mass concentrations of particulate matter (PM) ≤2.5 μm or ≤10 μm in aerodynamic diameter (PM2.5 and PM10, respectively). A number of research papers [1,2,3,4,5] have been published that examine the exposure and risk of Polycyclic Aromatic Hydrocarbons (PAHs) and their association with PM2.5, PM10 and ultrafine particles (UFPs). Many PAHs are known carcinogens [6,7,8]. The US Environmental Protection Agency (EPA), whose role is to safeguard the population and the environment, has published both inhalation and oral chronic dose exposure estimates associated for PAHs [9].
A relatively new area of focus in US EPA air quality research is measuring pollutants near roadways. It has been estimated that approximately 11% of households in the United States are located within 100 m of four-lane highways or expressways [10]. In the past decade, studies have been conducted both nationally and internationally which focus on particles and gases that are emitted from mobile source exhaust from busy highways and freeways. The first major study [11] was conducted in the United States in the Los Angeles Basin. Following the Los Angeles study, a number of researchers [12,13,14,15] have found that mobile sources on freeways can be a major source of fine and ultrafine PM and PAHs have been found in the fine and ultrafine particles fractions [16,17,18].
The field study was conducted to: (1) yield 8-h integrated particle-bound PAH data from low flow particulate samplers located in close proximity (within 15 m) to a major roadway (Interstate 40); (2) compare the data against traffic data that was also collected at the monitoring station; (3) create wind roses from the wind vector data collected at the monitoring location and analyze the speciated PAHs against local sources; (4) compare the data against traffic data that was also collected at the monitoring station; and (5) compare and contrast the PAH data to photochemical oxidant measurements being analyzed at this monitoring site and draw associations and conclusions from that comparison.

2. Experiment

US EPA and the North Carolina Department of Environment and Natural Resources operate an air pollution monitoring station to meet the requirements for a fixed NO2 near-road monitoring site. Figure 1 illustrates the location of the Research Triangle Park Near-Roadway station in relation to Raleigh, Durham and Chapel Hill, North Carolina. The inset shows the proximity of the station to the interstate. The fence of the monitoring stations is ~15 m from the edge of the roadway. The sampling occurred between 5 September and 6 November 2014, on a one-in-three day sampling schedule.
Table 1 illustrates the meteorological parameters during the study period. Please note that rainfall was intermittent during the sampling period with measurable rain occurring 7 of the 20 sampling days.
Sample collection was performed on 47 mm diameter Polytetrafluoroethylene (PTFE) filters. The filters were placed into low flow (~16.7 L/minute, BGI Incorporated model PQ200) discrete samplers with very sharp cut-point cyclones at aerodynamic size range of PM2.5. The samplers were mounted and operated along the freeway-facing fence inside the near roadway monitoring station. The inlets were positioned above the fenceline and had direct exposure to the interstate.
The sequential samplers were operated on three 8-h time slots. These were:
  • Sampler #1: 4 a.m.–12 p.m. (morning)
  • ampler #2: 12 p.m.–8 p.m. (afternoon)
  • Sampler #3: 8 p.m.–4 a.m., the next day. (nighttime)
The reasoning behind the staggered starting times was to capture the different “rush hour” commuting times between 6 and 10 a.m. and 4 and 8 p.m. on the highway. In addition, the sampling strategy allowed for the capture of the “nighttime” traffic when heavy duty diesel engines were expected to dominate the roadway. A total of 107 samples were collected. Of these 107 samples, 60 samples were collected using the 8-h samplers, seven field blanks were collected during the study and 40 samples were collected (i.e., two additional samplers) that were operated for 24 h. The 24 h samplers were considered to be the quality assurance samplers, which operated at the same time as the three 8-h samplers, i.e., 4 a.m. of one day to 4 a.m. of the next day.
In a temperature and humidity controlled laboratory, each sample filter was placed into a cassette and transported to the field using an aluminum cassette holder. The sample cassettes were loaded into the samplers and the time/date were entered and recorded in a field notebook. After each sampling event, the samples were removed from the samplers and transported in a temperature controlled container to a laboratory facility on the EPA campus in Research Triangle Park, North Carolina, where they were removed from the filter cassettes, placed in petri dishes and stored in a refrigerator at ~5 °C. The samples were stored in the refrigerator until the end of the sampling period and transported to North Carolina State University Chemistry Laboratory in Raleigh, North Carolina for analytical analysis.
Prior to the analysis, National Institute of Standards and Technology (NIST) traceable standards were obtained for the compounds listed in Table 2. Several researchers [17,18,19,20,21] provided details on the GC-MS analyses. The analysis methods utilized by these researchers provided a starting point for the temperature profile used for the GC-MS analyses for this project. However, it should be noted that each GC-MS is different and modifications to these methods were made until the NIST traceable standards eluted independently and illustrated excellent peak height and shape. In preparation for the GC-MS analysis, the filters were removed from the petri dishes and placed into 20-mL extraction vials. To each vial, 15 mL of dichloromethane was added. Each filter remained in the capped vial for 48 h. The aliquot was reduced to 2 mLs using steam bath in a fume hood. After the GC-MS was tuned, 1 µL of each aliquot was injected into an Agilent 6890 Series GC System coupled with an Agilent 5973 Network Mass Selective detector equipped with a J&W Scientific/Agilent Technologies DB-5 GC column with a helium carrier gas flow rate of 1 mL/min. The MS scan range was 50–350 mass to charge ratio (m/z). All chromatograms obtained from the samples were analyzed and cross-referenced against two mass spectral libraries in order to identify the compounds in the sample.

3. Results

3.1. Analysis of PAHs versus Wind Wind Speed and Wind Direction Vectors

Wind roses were generated using the wind speed and wind direction vectors data that were collected at the monitoring location. As can be seen from Figure 2, the interstate travels from northwest to southeast. The RDU international airport lies between northeast to east directions. Figure 2 shows the pollutant rose for the three sampling time periods: morning, afternoon and nighttime.
Figure 3a shows the trend plots of the sum of measured PAHs vs. Number of vehicles >60 feet in length (i.e., heavy duty diesel engine vehicles) during the afternoon (12 to 8:00 p.m.) on weekdays; Figure 3b shows the number of vehicles >60 feet in length during the afternoon on weekends. We can conclude that when the wind direction is from the interstate to the measurement site i.e., afternoon there is a positive correlation with traffic (>60 feet) intensity. Similarly, during the night the airport and the traffic interchanges around it are the major contributors to the nighttime PAHs.

3.2. Analysis of Traffic Patterns

The overall average daily traffic (ADT) on the 20 sample days is ~146,000 vehicles per day. The average speed of the vehicles on these days was ~70 miles per hour. The distribution of the vehicles is skewed heavily toward vehicles that are 10–30 feet in length. The next largest group (during the morning and nighttime periods) are the vehicles that are greater than 60 feet in length (diesel engine vehicles). The second largest group in the afternoon period was the vehicles in the <10 feet in length. Table 3 illustrates the distribution of the vehicles in the 6 different size categories.
As can be seen from Table 3, ~90% of all vehicles are between 10 and 30 feet in length. The afternoon period, between 12 and 8 p.m. has the highest number of vehicles. The vehicles between 10 and 30 feet dominate during all three periods: 89.6%, 89.7% and 89.6%. There are some deviations in the other vehicles classes; the most significant deviation is during the nighttime period for the vehicles >60 feet in length. These vehicles account for 2%–3% of the morning and afternoon traffic, but make up 5.6% when measured against the total for the nighttime traffic.

3.3. Analysis of PAHs versus Pollutant Data

Figure 4 illustrates the sum of the measured PAHs versus the afternoon (12 to 8 p.m.) photochemically active pollutants, NO, NO2 and O3. This time window provides the best estimate of the results of photochemical activity. Research suggests [22,23,24,25,26,27] that PAHs can react with NO, NO2 and O3. By examining Figure 4, correlations can be observed between the sum of the PAHs with NO, NO2 and O3. A linear relationship can be seen between the PAHs and the pollutant data. Although there are correlations (R2) between the NO, NO2 and O3 and sum of the measured PAHs (0.1, 0.04 and 0.07, respectively) there is discernable downward trend to the three graphs: as the pollutant concentrations increase, the sum of the PAHs decreases. In order to determine whether there is a significant relationship between the sum of the PAHs and the pollutant gases, an ANOVA regression was performed on the sum of the measured PAHs versus the three photochemical oxidants for the afternoon time period. With the alpha set at 5% (α = 0.05), the p-values were calculated for the three gas pollutants against the sum of the measured PAHs. For an ANOVA statistical analysis, if the p-value that is returned is less than 0.05, then the relationship between the two data sets is considered significant. The p-value are 0.000264, 0.000496, and 0.00613, for NO, NO2 and, O3 respectively, which are all less than 0.05. These findings suggest that there is a weak, yet significant relationship between these two oxides of nitrogen species and ozone and that as the gas concentrations in the atmosphere increase, the overall concentration of the PAHs decrease, suggesting that these pollutant gases are interacting with PAHs and that the PAHs in the atmosphere are being chemically removed.

4. Discussion

Figure 5 illustrates the results of this study compared to other published studies. Data from this research study compared well with data from other research studies [28,29,30,31,32,33,34]. The sum of the concentrations of PAHs in rural, suburban and urban locations ranges between 0.5 and 20 ng/m3. The sum of the PAH concentrations from this study was 160 ng/m3. A similar research study [34] performed at a busy intersection in Tainan, Taiwan, showed very high sum of the PAHs, ~667 ng/m3.

5. Conclusions

This study provides a convenient methodology for collecting, extracting and analyzing for particle bound PAHs in three 8-h periods (morning, afternoon and nighttime) within a 24-h period. The results (0.1–21.6 nanogram/cubic meter ±9.0 std) agree with the published research literature (0.1 to 193.6 ng/m3) both nationally and internationally. There is a weak yet significant correlation between the PAHs with atmospheric oxidants. The distribution of the PAHs varied in relationship to the time of day. For afternoon hours, the PAH sources point to the interstate automobile emissions.
The published research studies focused on collection, analysis and interpretation of samples that were collected for 24-h periods or longer. Some rural studies collected samples over several days in order to collect enough sample for analysis. This study illustrated that if the sampling is close to the source, PAHs can be collected in 8-h segments using low flow (~16.7 lpm) PM2.5 samplers and source apportionment can be determined if meteorological data are available in the area.

Acknowledgments

The authors would like to thank Yang Zhang, North Carolina State University, Marine, Earth, and Atmospheric Sciences (MEAS); John Walker, EPA-Office of Research and Development (ORD), Research Triangle Park, North Carolina; Walter Robinson, Dept. Head North Carolina State University, MEAS; Sue Kimbrough, EPA-ORD, Richard Snow, EPA-ORD, Morteza Khaledi, Dept. Head North Carolina State University, Chemistry Department, Danielle Lehman, North Carolina State University, Chemistry Department Mass Spectrometry Lab. Dennis Mikel also would like to thank the EPA-ORD for providing access to the near-roadway station and use of the PM2.5 samplers during this study.

Author Contributions

Dennis K. Mikel conceived, designed and performed the experiment, analyzed the data and contributed reagents/materials/data analysis tools as part of his MS research. Dennis K. Mikel and Viney P. Aneja wrote the paper.

Conflicts of Interest

The authors declare no conflict of interest. The funding sponsors had no role in the design of the study; in the collection, analyses, or interpretation of data; in the writing of the manuscript, and in the decision to publish the results.

Abbreviations

The following abbreviations are used in this manuscript:
PAHsPolycyclic Aromatic Hydrocarbons
PM2.5Particulate Matter ≥2.5 microns in aerodynamic diameter
PM10Particulate Matter ≥10 microns in aerodynamic diameter
ANOVAAnalysis of Variance
UFPUltrafine Particulate
EPAUnited States Environmental Protection Agency
NONitric Oxide
NO2Nitrogen Dioxide
O3Ozone
GC-MSGas Chromatography-Mass Spectrometry
NISTNational Institute of Standards and Technology
ADTAverage Daily Traffic
R2R-squared, the correlation coefficient of a linear equation
ng/m3nanograms per cubic meter
RDURaleigh-Durham International Airport
μLmicroliter
lpmliters per minute
mLmilliliters
nmnanometers

References

  1. Vyskocil, A.; Fiala, Z.; Chenier, V.; Krajak, L.; Ettlerova, E.; Bukac, J.; Viau, C.; Emminger, S. Assessment of multipathway exposure of small children to PAH. Environ. Toxicol. Pharmacol. 2000, 8, 111–118. [Google Scholar] [CrossRef]
  2. Rajput, N.; Lakhani, A. PAHs and their carcinogenic potencies in diesel fuel and diesel generator exhaust. Hum. Ecol. Risk Assess. 2009, 15, 201–213. [Google Scholar] [CrossRef]
  3. Jyethi, D.S.; Khillare, P.; Sarkar, S. Risk assessment of inhalation exposure to polycyclic aromatic hydrocarbons in school children. Environ. Sci. Pollut. Res. 2014, 21, 366–378. [Google Scholar] [CrossRef] [PubMed]
  4. Seagrave, J.; Gigliotti, A.; McDonald, J.; Seilkop, S.; Whitney, K.; Zielinska, B.; Mauderly, J. Composition, toxicity, and mutagenicity of particulate and semivolatile emissions from heavy-duty compressed natural gas powered vehicles. Toxicol. Sci. 2005, 87, 232–241. [Google Scholar] [CrossRef] [PubMed]
  5. Fromme, H.; Oddoy, A.; Piloty, M.; Krause, M.; Lahrza, T. Polycyclic aromatic hydrocarbons PAH and diesel engine emission elemental carbon inside a car and a subway train. Sci. Total Environ. 1998, 217, 165–173. [Google Scholar] [CrossRef]
  6. Melendez-Colon, V.J.; Luch, A.; Seidel, A.; Baird, W. Cancer initiated by polycyclic aromatic hydrocarbons results from formation of stable DNA adducts rather than apurinic sites. Carcinogenesis 1999, 20, 1885–1891. [Google Scholar] [CrossRef] [PubMed]
  7. Bonner, M.; Han, D.; Nie, J.; Rogerson, P.; Vena, J.; Muti, P.; Freudenheim, J. Breast cancer risk and exposure in early life to polycyclic aromatic hydrocarbons using total suspended particulates as a proxy measure. Cancer Epidemiol. Biomark. Preview 2005, 14, 53–60. [Google Scholar]
  8. Nie, J.; Beyea, J.; Bonner, M.; Han, D.; Vena, J.; Rogerson, P.; Vito, D.; Muti, P.; Trevisan, M.; Edge, S.; et al. Exposure of traffic emissions throughout life and risk of breast cancer: The Western New York Exposures and Breast Cancer (WEB) study. Cancer Causes Control 2007, 18, 947–955. [Google Scholar] [CrossRef] [PubMed]
  9. Environmental Protection Agency. Risk Assessment for Carcinogens. Available online: http://www2.epa.gov/fera/risk-assessment-carcinogens (accessed on 15 January 2016).
  10. Brugge, D.; Durant, J.; Rioux, C. Near-highway pollutants in motor vehicle exhaust: A review of epidemiologic evidence of cardiac and pulmonary health risks. Environ. Health 2007, 6, 23–25. [Google Scholar] [CrossRef] [PubMed]
  11. Zhu, Y.; Hinds, W.; Kim, S.; Sioutas, C. Concentration and size distribution of ultrafine particles near a major highway. J. Air Waste Manag. Assoc. 2002, 9, 1032–1042. [Google Scholar] [CrossRef]
  12. Sioutas, C.; Delfino, R.; Singh, M. Exposure assessment for atmospheric ultrafine particles (UFPs) and Implications in epidemiologic research. Environ. Health Perspect. 2005, 113, 947–955. [Google Scholar] [CrossRef] [PubMed]
  13. Hagler, G.; Baldauf, R.; Thoma, E.; Long, T.; Snow, R.; Kinsey, J.; Oudejans, L.; Gullett, B. Ultrafine particles near a major roadway in Raleigh, North Carolina: Downwind attenuation and correlation with traffic-related pollutants. Atmos. Environ. 2009, 43, 1229–1234. [Google Scholar] [CrossRef]
  14. Kim, S.; Shen, S.; Sioutas, C.; Zhu, Y.; Hinds, W. Size distribution and diurnal and seasonal trends of ultrafine particles in source and receptor sites of the Los Angeles basin. J. Air Waste Manag. Assoc. 2002, 52, 297–307. [Google Scholar] [CrossRef] [PubMed]
  15. Shi, J.; Evans, D.; Khan, A.; Harrison, R. Sources and concentration of nanoparticles (10 nm diameter) in the urban atmosphere. Atmos. Environ. 2001, 35, 1193–1202. [Google Scholar] [CrossRef]
  16. Maciejczyk, P.B.; Offenberg, J.; Clemente, J.; Blaustein, M.; Thurston, G.; Chen, L. Ambient pollutant concentrations measured by a mobile laboratory in South Bronx, NY. Atmos. Environ. 2004, 38, 5283–5294. [Google Scholar] [CrossRef]
  17. Gigliotti, C.L.; Dachs, I.; Nelson, E.; Brunciak, P.; Eisenreich, S. Polycyclic aromatic hydrocarbons in the New Jersey Coastal Atmosphere. Environ. Sci. Technol. 2000, 34, 3547–3554. [Google Scholar] [CrossRef]
  18. Pleil, J.; Vette, A.; Rappaport, S. Assaying particle bound polycyclic aromatic hydrocarbons from archived PM2.5 filters. J. Chromatogr. 2003, 1033, 9–17. [Google Scholar] [CrossRef]
  19. Li, Z.; Sjodin, A.; Porter, E.; Patterson, D.; Needham, L.; Lee, S.; Russell, A.; Mulholland, J. Characterization of PM2.5-bound polycyclic aromatic hydrocarbons in Atlanta. Atmos. Environ. 2009, 43, 1043–1050. [Google Scholar] [CrossRef]
  20. Chen, S.-J.; Hwang, P.-S.; Hsieh, L.-T. The height variation and particle size distribution of polycyclic aromatic hydrocarbons in the ambient air. Toxicol. Environ. Chem. 1997, 60, 111–128. [Google Scholar] [CrossRef]
  21. Allen, A.G.; da Rocha, G.; Cardoso, A.; Machado, W.P.C.; de Andrade, J. Atmospheric particulate polycyclic aromatic hydrocarbons from road transport in southeast Brazil. Transp. Res. 2008, 13, 483–490. [Google Scholar] [CrossRef]
  22. Butler, J.; Crossley, P. Reactivity of Polycyclic Aromatic Hydrocarbons absorbed on soot particles. Atmos. Environ. 1980, 15, 91–94. [Google Scholar] [CrossRef]
  23. Feilberg, A.; Poulson, M.; Nielsen, T.; Skov, H. Occurrence and sources of particulate nitro-polycyclic aromatic hydrocarbons in ambient air in Denmark. Atmos. Environ. 2001, 35, 353–366. [Google Scholar] [CrossRef]
  24. Bamford, H.; Baker, J. Nitro-polycyclic aromatic hydrocarbon concentrations and sources in urban and suburban atmospheres of the mid-Atlantic region. Atmos. Environ. 2003, 37, 2077–2091. [Google Scholar] [CrossRef]
  25. Pitts, J.N.; van Cauwenberghe, K.; Grosjean, D.; Schmid, J.; Fitz, D.; Belser, W.; Knudson, G.; Hynds, P. Atmospheric reactions of polycyclic aromatic hydrocarbons: Facile formation of mutagenic nitro derivatives. Science 1978, 202, 515–519. [Google Scholar] [CrossRef] [PubMed]
  26. Nikolaou, K.; Masclet, P.; Mouvier, G. Sources and chemical reactivity of polynuclear aromatic hydrocarbons in the atmosphere—A critical review. Sci. Total Environ. 1984, 32, 103–132. [Google Scholar] [CrossRef]
  27. Kormacher, W.; Mamantov, G.; Wehry, E.; Natush, D. Resistance to photochemical decomposition of polycyclic aromatic hydrocarbons, vapor-adsorbed on coal fly ash. Environ. Sci. Technol. 1980, 14, 1094–1099. [Google Scholar] [CrossRef]
  28. Gao, B.; Yu, J.-Z.; Li, S.-X.; Ding, X.; He, Q.-F.; Wang, X.-M. Roadside and rooftop measurements of polycyclic aromatic hydrocarbons in PM2.5 in urban Guangzhou: Evaluation of vehicular and regional combustion source contributions. Atmos. Environ. 2011, 45, 7184–7191. [Google Scholar] [CrossRef]
  29. Bourotte, C.; Forti, M.; Taniguchi, S.; Bicego, M.; Lotufo, P. A wintertime study of PAHs in fine and coarse aerosols in Sao Paulo city, Brazil. Atmos. Environ. 2005, 39, 3799–3811. [Google Scholar] [CrossRef]
  30. Li, J.; Zhang, G.; Li, X.; Qi, S.; Liu, G.; Peng, X. Source seasonality of polycyclic aromatic hydrocarbons (PAHs) in a subtropical city, Guangzhou, South China. Sci. Total Environ. 2006, 355, 145–155. [Google Scholar] [CrossRef] [PubMed]
  31. Eiguren-Fernandez, A.; Miguel, A.; Froines, J.; Thurairatnam, S.; Avol, E. 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]
  32. Tsapakis, M.; Stephanou, E. Polycyclic aromatic hydrocarbons in the atmosphere of the Eastern Mediterranean. Environ. Sci. Technol. 2005, 39, 6584–6590. [Google Scholar] [CrossRef] [PubMed]
  33. Tsapakis, M.; Stephanou, E. Occurrence of gaseous and particulate poly-cyclic aromatic hydrocarbons in the urban atmosphere: Study of sources and ambient temperature effect on the gas/particle concentration and distribution. Environ. Pollut. 2005, 133, 147–156. [Google Scholar] [CrossRef] [PubMed]
  34. Shue, H.-L.; Lee, W.-J.; Lin, S.; Guor-Cheng, F.; Chang, H.-C.; You, W.-C. Particle-bound PAH content in ambient air. Environ. Pollut. 1997, 96, 369–382. [Google Scholar] [CrossRef]
Atmosphere 07 00131 g001 550
Figure 1. The monitoring location in relation to three major cities (Raleigh, Durham and Chapel Hill) in North Carolina with the insert showing the monitoring site’s proximity to the interstate.
Figure 1. The monitoring location in relation to three major cities (Raleigh, Durham and Chapel Hill) in North Carolina with the insert showing the monitoring site’s proximity to the interstate.
Atmosphere 07 00131 g001
Atmosphere 07 00131 g002a 550Atmosphere 07 00131 g002b 550
Figure 2. Pollutant Rose for (a) morning; (b) afternoon; and (c) night time 8-h samples.
Figure 2. Pollutant Rose for (a) morning; (b) afternoon; and (c) night time 8-h samples.
Atmosphere 07 00131 g002aAtmosphere 07 00131 g002b
Atmosphere 07 00131 g003 550
Figure 3. Trend plots of the sum of measured PAHs vs. (a) number of vehicles >60 feet in length during the afternoon on weekdays; (b) number of vehicles >60 feet length during on weekends (+/1 Std as indicated).
Figure 3. Trend plots of the sum of measured PAHs vs. (a) number of vehicles >60 feet in length during the afternoon on weekdays; (b) number of vehicles >60 feet length during on weekends (+/1 Std as indicated).
Atmosphere 07 00131 g003
Atmosphere 07 00131 g004 550
Figure 4. The afternoon sum of measured PAHs vs. (a) NO; (b) NO2; and (c) O3 concentrations (+/1 Std as indicated).
Figure 4. The afternoon sum of measured PAHs vs. (a) NO; (b) NO2; and (c) O3 concentrations (+/1 Std as indicated).
Atmosphere 07 00131 g004
Atmosphere 07 00131 g005 550
Figure 5. Comparison of study PAHs to values found in the literature.
Figure 5. Comparison of study PAHs to values found in the literature.
Atmosphere 07 00131 g005
Table
Table 1. Summary of the meteorological conditions during the sampling days.
Table 1. Summary of the meteorological conditions during the sampling days.
VariableWD Vector (Degrees)WS Vector (m/s)Temperature (°C)Relative Humdity (%)Rainfall (mm H2O)
Mean134.10.618.278.10.2
High358.52.630.198.11.8
Low10.90.17.735.70.0
Table
Table 2. Compounds, CAS numbers, physical characteristics.
Table 2. Compounds, CAS numbers, physical characteristics.
Compound NameCAS No.No. of RingsMolecular Weights
Naphthalene91-20-32128.2
Acenaphthene83-32-93154.2
Acenaphthylene206-96-83152.2
Fluorene86-73-73166.2
Phenanthrene85-01-83178.2
Anthracene120-12-73178.2
Fluorenone206-44-04180.2
Pyrene129-00-04202.3
Fluoranthene486-25-94202.3
Retene483-65-83212.3
Benzo (a) anthracene56-55-34228.3
Chrysene218-01-94228.3
Benzo (k) fluoranthene207-08-95252.3
Benzo (a) pyrene50-32-85252.3
Perylene198-55-05252.3
Benzo(e) pyrene192-97-25278.4
Dibenz (a,h) anthracene53-70-35276.3
Benzo (g,h,i) perylene191-24-26276.3
Indeno(1,2,3-cd)pyrene193-39-56276.3
Coronene191-07-17300.3
Table
Table 3. Distribution of the average daily traffic (ADT) for the three sampling periods.
Table 3. Distribution of the average daily traffic (ADT) for the three sampling periods.
<10 (feet)10–30 (feet)30–40 (feet)40–50 (feet)50–60 (feet)>60 (feet)Total
MorningAverage129352,3011759786388181658,344
Percent2.2%89.6%3.0%1.4%0.7%3.1%
AfternoonAverage250063,1091960901377152470,373
Percent3.6%89.7%2.8%1.3%0.5%2.2%
NighttimeAverage25112,6922231259178814,169
Percent1.8%89.6%1.68%0.9%0.6%5.6%

Share and Cite

MDPI and ACS Style

Mikel, D.K.; Aneja, V.P. Measurements and Analysis of Polycyclic Aromatic Hydrocarbons near a Major Interstate. Atmosphere 2016, 7, 131. https://doi.org/10.3390/atmos7100131

AMA Style

Mikel DK, Aneja VP. Measurements and Analysis of Polycyclic Aromatic Hydrocarbons near a Major Interstate. Atmosphere. 2016; 7(10):131. https://doi.org/10.3390/atmos7100131

Chicago/Turabian Style

Mikel, Dennis K., and Viney P. Aneja. 2016. "Measurements and Analysis of Polycyclic Aromatic Hydrocarbons near a Major Interstate" Atmosphere 7, no. 10: 131. https://doi.org/10.3390/atmos7100131

Note that from the first issue of 2016, this journal uses article numbers instead of page numbers. See further details here.

Article Metrics

Back to TopTop