Sources and atmospheric chemistry of oxy- and nitro-PAHs in the ambient air of Grenoble (France)

Tomaz, Sophie; Jaffrezo, Jean-Luc; Favez, Olivier; Villenave, Éric; Albinet, Alexandre

doi:10.1016/j.atmosenv.2017.04.042

Cited by 65 publications

(62 citation statements)

References 87 publications

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“…Regarding to other chemicals, the environmental levels of Σ 8 Quinones were found in the range of 1.36-12.23 ng m −3 . The most abundant quinone in both phases was 1,4-phenanthrenequinone, which has been reported as a direct emission marker [74]. In the gas phase, quinones represent about 58% of the collected emissions.…”

Section: Organic Components As Emission Indicators (Polycyclic Aromatmentioning

confidence: 81%

Air Pollution in an Urban Area of Mexico: Sources of Emission (Vehicular, Natural, Industrial, and Brick Production)

Ojeda-Castillo¹,

Alonso-Romero²,

Mena³

et al. 2019

Air Pollution - Monitoring, Quantification and Removal of Gases and Particles

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In recent years, the interest in aerosol particles has increased due to concerns about the effects on human health. The study of the chemical characterization (organic matter, sulfates, nitrates, and black carbon) has improved the knowledge about the negative contribution of chemicals to the environment. The identification of secondary processes (from pollutants such as SO 2 , NO x , and PAHs) and their role when combined with environmental factors such as humidity, solar radiation, and temperature are also of interest. With this background, this chapter seeks to highlight the most recent findings on the chemical composition of aerosol particles in the ambient air of one of the main cities of Mexico: the Metropolitan Area of Guadalajara. This megalopolis has almost 60% of the population of the Jalisco state, approximately 2.2 million vehicles and an extensive artisan brick production. Furthermore, due to its geographical position, it experiences frequent episodes of thermal inversion and exposition to high levels of solar radiation, mainly during the first half of the year.

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Section: Organic Components As Emission Indicators (Polycyclic Aromatmentioning

confidence: 81%

Air Pollution in an Urban Area of Mexico: Sources of Emission (Vehicular, Natural, Industrial, and Brick Production)

Ojeda-Castillo¹,

Alonso-Romero²,

Mena³

et al. 2019

Air Pollution - Monitoring, Quantification and Removal of Gases and Particles

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“…In contrast, during nighttime, the phenanthrenequinones are mainly products of reactions with nitrate radicals that proceed from reactions involving NO 2 and O 3 [87]. The influence of WS suggests that the secondary transformation also may occur during the transport of air masses [16], as reported for the 90% formation of 9,10-PQ during transport in Los Angeles, California [88]. the secondary transformation also may occur during the transport of air masses [16], as reported for the 90% formation of 9,10-PQ during transport in Los Angeles, California [88].…”

Section: Possible Sourcesmentioning

confidence: 99%

“…The influence of WS suggests that the secondary transformation also may occur during the transport of air masses [16], as reported for the 90% formation of 9,10-PQ during transport in Los Angeles, California [88]. the secondary transformation also may occur during the transport of air masses [16], as reported for the 90% formation of 9,10-PQ during transport in Los Angeles, California [88]. highlighting the influence of secondary formation upon the 1,4-AQ levels observed within the GMA.…”

Section: Possible Sourcesmentioning

confidence: 99%

“…Additionally, Chen et al [8] suggested that, with smaller particle size, PM 1 is more harmful than PM 2.5 . Despite this, ambient levels and distribution of quinones have been determined mainly in PM 10 [9][10][11] and total suspended particles [12,13], while few studies have addressed those in the gas phase and fine particles simultaneously [14][15][16].…”

Section: Introductionmentioning

confidence: 99%

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Observed Daily Profiles of Polyaromatic Hydrocarbons and Quinones in the Gas and PM1 Phases: Sources and Secondary Production in a Metropolitan Area of Mexico

et al. 2019

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The diel variation of meteorological conditions strongly influences the formation processes of secondary air pollutants. However, due to the complexity of sampling highly reactive chemical compounds, significant information about their transformation and source can be lost when sampling over long periods, affecting the representativeness of the samples. In order to determine the contribution of primary and secondary sources to ambient levels of polyaromatic hydrocarbons (PAHs) and quinones, measurements of gas and PM1 phases were conducted at an urban site in the Guadalajara Metropolitan Area (GMA) using a 4-h sampling protocol. The relation between PAHs, quinones, criteria pollutants, and meteorology was also addressed using statistical analyses. Total PAHs (gas phase + PM1 phase) ambient levels ranged between 184.03 ng m−3 from 19:00 to 23:00 h and 607.90 ng m−3 from 07:00 to 11:00 h. These figures both coincide with the highest vehicular activity peak in the morning and at night near the sampling site, highlighting the dominant role of vehicular emissions on PAHs levels. For the gas phase, PAHs ranged from 177.59 to 595.03 ng m−3, while for PM1, they ranged between 4.81 and 17.44 ng m−3. The distribution of the different PAHs compounds between the gas and PM1 phases was consistent with their vapour pressure (p °L) reported in the literature, the PAHs with vapour pressure ≤ 1 × 10−3 Pa were partitioned to the PM1, and PAHs with vapour pressures ≥ 1 × 10−3 Pa were partitioned to the gas phase. PAHs diagnostic ratios confirmed an anthropogenic emission source, suggesting that incomplete gasoline and diesel combustion from motor vehicles represent the major share of primary emissions. Quinones ambient levels ranged between 18.02 ng m−3 at 19:00–23:00 h and 48.78 ng m−3 at 15:00–19:00 h, with significant increases during the daytime. The distribution of quinone species with vapour pressures (p °L) below 1 × 10−4 Pa were primarily partitioned to the PM1, and quinones with vapour pressures above 1 × 10−4 Pa were mainly partitioned to the gas phase. The analysis of the distribution of phases in quinones suggested emissions from primary sources and their consequent degradation in the gas phase, while quinones in PM1 showed mainly secondary formation modulated by UV, temperature, O3, and wind speed. The sampling protocol proposed in this study allowed obtaining detailed information on PAHs and quinone sources and their secondary processing to be compared to existing studies within the GMA.

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“…Therefore, data from long sampling times and under high ozone ambient concentrations may be biased by sampling artefacts by more than 100 % (Schauer et al, 2003;Goriaux et al, 2006). However, at low ozone levels, negative artefacts were considered not significant (Tsapakis and Stephanou, 2003), whilst, at medium ozone levels (30-50 ppb), PAH values were underestimated by 30 % (Schauer et al, 2003). In addition, heterogeneous reactions during particle sampling may occur only on the monolayer surface coverage with limited diffusion of oxidants to the bulk particles (Keyte et al, 2013, and references therein).…”

Section: Data Analysis and Error Evaluationmentioning

confidence: 99%

Response to comments (SC1) by Alexandre Albinet

zein¹

2019

Preprint

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Ambient particulate matter (PM) can contain a mix of different toxic species derived from a wide variety of sources. This study quantifies the diurnal variation and nocturnal abundance of 16 polycyclic aromatic hydrocarbons (PAHs), 10 oxygenated PAHs (OPAHs) and 9 nitrated PAHs (NPAHs) in ambient PM in central Beijing during winter. Target compounds were identified and quantified using gas chromatography-time-of-flight mass spectrometry (GC-Q-ToF-MS). The total concentration of PAHs varied between 18 and 297 ng m −3 over 3 h daytime filter samples and from 23 to 165 ng m −3 in 15 h night-time samples. The total concentrations of PAHs over 24 h varied between 37 and 180 ng m −3 (mean: 97 ± 43 ng m −3 ). The total daytime concentrations during high particulate loading conditions for PAHs, OPAHs and NPAHs were 224, 54 and 2.3 ng m −3 , respectively. The most abundant PAHs were fluoranthene (33 ng m −3 ), chrysene (27 ng m −3 ), pyrene (27 ng m −3 ), benzo[a]pyrene (27 ng m −3 ), benzo[b]fluoranthene (25 ng m −3 ), benzo[a]anthracene (20 ng m −3 ) and phenanthrene (18 ng m −3 ). The most abundant OPAHs were 9,10-anthraquinone (18 ng m −3 ), 1,8-naphthalic anhydride (14 ng m −3 ) and 9-fluorenone (12 ng m −3 ), and the three most abundant NPAHs were 9-nitroanthracene (0.84 ng m −3 ), 3-nitrofluoranthene (0.78 ng m −3 ) and 3-nitrodibenzofuran (0.45 ng m −3 ).PAHs and OPAHs showed a strong positive correlation with the gas-phase abundance of NO, CO, SO 2 and HONO, indicating that PAHs and OPAHs can be associated with both local and regional emissions. Diagnostic ratios suggested emissions from traffic road and coal combustion were the predominant sources of PAHs in Beijing and also revealed the main source of NPAHs to be secondary photochemical formation rather than primary emissions. PM 2.5 and NPAHs showed a strong correlation with gas-phase HONO. 9-Nitroanthracene appeared to undergo a photodegradation during the daytime and showed a strong positive correlation with ambient HONO (R = 0.90, P < 0.001). The lifetime excess lung cancer risk for those species that have available toxicological data (16 PAHs, 1 OPAH and 6 NPAHs) was calculated to be in the range 10 −5 to 10 −3 (risk per million people ranges from 26 to 2053 cases per year).

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Sources and atmospheric chemistry of oxy- and nitro-PAHs in the ambient air of Grenoble (France)

Cited by 65 publications

References 87 publications

Air Pollution in an Urban Area of Mexico: Sources of Emission (Vehicular, Natural, Industrial, and Brick Production)

Air Pollution in an Urban Area of Mexico: Sources of Emission (Vehicular, Natural, Industrial, and Brick Production)

Observed Daily Profiles of Polyaromatic Hydrocarbons and Quinones in the Gas and PM1 Phases: Sources and Secondary Production in a Metropolitan Area of Mexico

Response to comments (SC1) by Alexandre Albinet

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