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Asian Journal of Atmospheric Environment - Vol. 15 , No. 1

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Asian Journal of Atmospheric EnvironmentVol. 15, No. 1
Abbreviation: Asian J. Atmos. Environ
ISSN: 1976-6912 (Print) 2287-1160 (Online)
Print publication date 31 Mar 2021
Received 18 Sep 2020 Revised 23 Nov 2020 Accepted 07 Dec 2020

Atmospheric Occurrence of Particle-associated Nitrotriphenylenes via Gas-phase Radical-initiated Reactions Observed in South Osaka, Japan
Takayuki Kameda* ; Hiroshi Bandow1)
Graduate School of Energy Science, Kyoto University, Yoshida-Honmachi, Sakyo-ku, Kyoto 606-8501, Japan
1)Department of Applied Chemistry, Graduate School of Engineering, Osaka Prefecture University, 1-1 Gakuen-cho, Naka-ku, Sakai 599-8531, Japan

Correspondence to : * Tel: +81-75-753-5621 E-mail:

Copyright © 2021 by Asian Association for Atmospheric Environment
This is an open-access article distributed under the terms of the Creative Commons Attribution Non-Commercial License (, which permits unrestricted non-commercial use, distribution, and reproduction in any medium, provided the original work is properly cited.
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Nitrotriphenylenes (NTPs), which include the highly mutagenic isomer 2-nitrotriphenylene (2-NTP), have been detected in airborne particles. From a public hygienic point of view, it is necessary to study the environmental occurrence of NTPs in detail. In this study, concentrations of five nitrated polycyclic aromatic hydrocarbons (nitro-PAHs) including NTPs in airborne particles and of nitrogen oxides (NOx; NO+NO2) and carbon monoxide (CO), at a location in South Osaka, Japan, were measured at 3 h intervals. It was found that the diurnal variations in the concentrations of 1-nitropyrene (1-NP), NOx, and CO were similar, being high early in the morning and late in the evening. This finding indicates that the occurrence of 1-NP is affected significantly by primary emissions, particularly by automotive emissions. The concentration change in 1-nitrotriphenylene was similar to that of 2-nitropyrene produced by an atmospheric OH radicalinitiated reaction. On the contrary, the variations in the concentrations of 2-nitrofluoranthene (2-NF) and 2-NTP were significantly different from those of the other nitro-PAHs, i.e., their concentrations increased during the nighttime, suggesting that neither 2-NF nor 2-NTP was emitted from the primary sources, but were formed via the NO3 radicalinitiated nitration of the parent fluoranthene and triphenylene (TP) in the atmosphere. Based on the ambient concentration of 2-NTP and the reported rate constant for the reaction of TP with NO3 radicals, the yield of 2-NTP from the gas-phase NO3 radical-initiated reaction of TP was estimated to be 23%.

Keywords: PAH, Nitroarene, Triphenylene, Secondary formation, Airborne particles


Most nitrated polycyclic aromatic hydrocarbons (nitro-PAHs), a class of polycyclic aromatic compounds (PACs), exhibit direct-acting mutagenicity or carcinogenicity (Durant et al., 1996). Some of them have been detected in particulate matters in the ambient air (Bamford and Baker, 2003) or combustion exhaust (Schuetzle et al., 1982). For example, 1-nitropyrene (1-NP) has been detected in both diesel exhaust particles (Schuetzle, 1983) and airborne particles (Feilberg et al., 2001). Although 1-NP can be formed from gas-particle phase heterogeneous reactions on a specific substrate such as mineral dust aerosols (Kameda et al., 2016) or under the high NO2 condition (Nguyen et al., 2009; Miet et al., 2004; Finlayson-Pitts and Pitts, 2000), atmospheric 1-NP is believed to originate predominantly from combustion processes (Bamford and Baker, 2003; Feilberg et al., 2001). In contrast, several types of nitro-PAHs are formed via gas-phase reactions of semi-volatile PAHs. For example, 2-nitropyrene (2-NP) and 2-nitrofluoranthene (2-NF) are formed by the gas-phase OH radicalinitiated reactions of pyrene (PYR) and fluoranthene (FLRA) in the presence of NO2 (Wilson et al., 2020; Atkinson and Arey, 1994; Atkinson et al., 1990; Arey et al., 1986). The reaction proceeds by the initial addition of the OH radicals to PYR or FLRA, followed by the addition of NO2 and loss of H2O. A similar mechanism for the gas-phase NO3 radical reaction with FLRA produces 2-NF upon the loss of HNO3 (Atkinson and Arey, 1994; Atkinson et al., 1990; Arey et al., 1986). Triphenylene (TP), which is less volatile than FLRA (Finlayson-Pitts and Pitts, 2000), also reacts with OH and/or NO3 radicals in the gas-phase, resulting in nitrotriphenylenes (NTPs) (Zimmermann et al., 2012; Kameda et al., 2006), which include the strong mutagenic isomer 2-nitrotriphenylene (2-NTP) (Ishii et al., 2001, 2000). The rate constants for the gas-phase reactions of TP with OH or NO3 radicals have been determined by a relative-rate technique in a CCl4 liquidphase system (Kameda et al., 2013). Because strongly mutagenic 2-NTP has been found in the air at concentrations comparable to those of 1-NP and 2-NF, which are the most abundant airborne nitro-PAHs (Zimmermann et al., 2012; Kameda et al., 2006; Kawanaka et al., 2005; Kameda et al., 2004; Ishii et al., 2001; Ishii et al., 2000), its contribution to the mutagenicity of airborne particles is expected to be significant. However, it is difficult to understand the factors influencing the formation and behaviour of atmospheric NTPs, because they are produced from not only the gas-phase radical-initiated reactions but also gas-solid-phase heterogeneous reactions of TP with NO2/NO3/N2O5 (Yang et al., 2013; Ishii et al., 2000) and combustion of organic matters such as fossil fuels (Zimmermann et al., 2012; Kameda et al., 2006). From a public hygienic point of view, the acquisition of more detailed data about the environmental occurrence of NTPs is of great importance.

In the present study, we sampled airborne particles at a point in South Osaka, Japan at 3-hr intervals, and determined the particle-associated NTPs, other typical nitro-PAHs, and gaseous atmospheric pollutants simultaneously in order to understand the factors controlling the occurrence and concentrations of atmospheric NTPs.

2. 1 Sampling of Airborne Particles

Airborne particulates were collected on quartz fiber filters (Advantec MFS, QR100) using high-volume air samplers (Kimoto Electrics, Model 120) on the rooftop of a three-story building (approximately 10 m above the ground level) at Osaka Prefecture University in Sakai, Osaka, Japan (34°55ʹN, 135°51ʹE). The sampling site was located in a slightly polluted residential area in South Osaka, which can be regarded as a typical suburban area in Japan. Vehicular traffic on moderately busy roads, Route 310 and Hanwa-Highway, 200 m and 2 km away from the sampling site, respectively, was the only substantial source of air pollutants; no other significant potential stationary source of air pollution was paresent near the site. Air samples were collected at intervals of 3 h over two 27-hr periods: (I) September 4 and 5, 2001 and (II) November 28 and 29, 2001. The average air collection rate of the air samplers was 1.5 m3 min-1 and no cut-off stage was employed. The filter samples were stored at 253 K until they were subjected to the analysis.

2. 2 Chemical Analysis of Nitro-PAHs

The filter samples were cut into fine pieces, and all the fine pieces were put into 200 mL of benzene/ethanol (3/1, v/v). Soluble organic fractions (SOF) was extracted by sonication for 15 min twice, then the extract solution was filtered to remove solid substances with cellulose acetate filter (Advantec MFS, No.2). The filtrate was washed with 100 mL of 5% sodium hydroxide, 100 mL of 20% (v/v) sulfuric acid and 100 mL of water. After evaporating the organic layer to ca. 5 mL and filtered with a 0.22 μm membrane filter, the solvent was gently removed with a nitrogen stream. A 0.5 mL sample solution was obtained by adding methanol to the residue. An aliquot of the sample solution was injected into the HPLC system. The HPLC system with column-switching and chemiluminescence detection was employed for nitro-PAHs quantification as reported previously (Kameda et al., 2006; Kameda et al., 2004). Although nitro-PAHs are not fluorescent, they are metal-catalytically reduced to strongly fluorescent amino-PAHs in the HPLC system, enabling a sensitive and selective detection of nitro-PAHs by the chemiluminescence detector. For the calibration curves of the standard nitro-PAHs, the chemiluminescence intensities were proportional to the concentrations of the compounds up to 2000 fmol per injection, and the calibration curves showed good linearity (r>0.999). The quantification limits of the HPLC system employed for 1-NP, 2-NP, 2-NF, 1-nitrotriphenylene (1-NTP), and 2-NTP were 2, 20, 10, 75, and 60 fmol, respectively (S/ N=3). Chemical structures of the target nitro-PAHs in this study are summarized in Table 1 with the information of their atmospheric sources.

Table 1. 
Structures of nitro-PAHs observed in this study and their atmospheric sources.
Nitro-PAHs Atmospheric Sources
Primary emission from combustion sources
Gas-solid-phase heterogeneous reaction
(minor contribution)
1-nitropyrene (1-NP)
Gas-phase OH radical-initiated reaction
2-nitropyrene (2-NP)
Gas-phase OH radical-initiated reaction
Gas-phase NO3 radical-initiated reaction
2-nitrofluoranthene (2-NF)
Primary emission from combustion sources
Gas-solid-phase heterogeneous reaction
Gas-phase OH radical-initiated reaction
1-nitrotriphenylene (1-NTP)
Primary emission from combustion sources
Gas-solid-phase heterogeneous reaction
Gas-phase OH radical-initiated reaction
Gas-phase NO3 radical-initiated reaction
2-nitrotriphenylene (2-NTP)

2. 3 Gas Analysis

During the sampling period, typical gaseous pollutants, namely, NOx (NO and NO2), and CO were monitored with a chemiluminescence NOx analyzer (Thermo Electron, MODEL 42s) and an NDIR CO analyzer (Thermo Electron, MODEL 48), respectively.

2. 4 Chemicals

1-NP was obtained from Sigma-Aldrich Co; 1-NTP and 2-NTP were obtained from Hayashi Pure Chemical Ind. Ltd. and ChemBridge Co., respectively; and 2-NF and 2-NP were purchased from Chiron AS. All the solvents and other chemicals used were HPLC or analytical grades from Wako Pure Chemical Ind., Ltd.


Table 2 shows the concentrations of selected inorganic gases and nitro-PAHs in 3-hr averaged samples of the airborne particles obtained in this study. The diurnal change of 1-NP in airborne particles collected between November 28 and 29 (abbreviated as Nov 28-29) is shown in Fig. 1a with the concentrations of NOx (=NO+NO2) and CO, which were measured during the same period of time. The concentrations of NOx and CO were in the ranges from 13 to 53 ppbv and from 0.6 to 1.3 ppmv, respectively. These concentrations can be regarded as normal for residential areas with slight pollution in Japan (Morikawa et al., 1997) and the observed concentrations of 1-NP associated with airborne particles (29-96 fmol m-3) were comparable to values reported by other researchers in Japan (Kamiya et al., 2017; Kojima et al., 2010a; Ishii et al., 2001), Hong Kong (Ma et al., 2016), New Zealand (Kalisa et al., 2019), and Czech Republic (Nežiková et al., 2020). The diurnal variations in concentrations of particle-associated 2-NF, 2-NP, 1-NTP, and 2-NTP on Nov 28-29 are shown in Fig. 1b. The concentration of 2-NF ranged from 33 fmol m-3 for the sample collected between 12:00 and 15:00 (abbreviated as 12:00) to 412 fmol m-3 for the sample collected at 0:00. The concentration of the 2-NF obtained in this study is substantially the same as the previously reported levels in Japan (Kamiya et al., 2017; Kojima et al., 2010a; Kojima et al., 2010b), France (Albinet et al., 2007), and Italy (Di Filippo et al., 2010). The concentration of 2-NTP was also the lowest (10 fmol m-3) at 12:00 and reached the maximum (43 fmol m-3) at 0:00. On the contrary, the highest concentrations of 1-NTP and 2-NP were observed at 18:00. The concentrations of 1-NTP and 2-NP were in the ranges from 8 to 72 fmol m-3 and from 21 to 86 fmol m-3, respectively. The observed concentration of 2-NP in airborne particles was slightly higher than that measured previously in Japan (Kamiya et al., 2017; Murahashi et al., 1999), France (Ringuet et al., 2012), and Italy (Di Filippo et al., 2010). While the concentrations of 1-NTP and 2-NTP obtained in this study were lower than previously reported levels in Tokyo, Japan (Ishii et al., 2001; Ishii et al., 2000), these values were slightly higher than those reported in Riverside, CA and Mexico City, Mexico (Zimmermann et al., 2012). The diurnal variations in the concentrations of NOx, CO, and 1-NP, which are primarily emitted from the combustion processes, were similar, i.e., their concentrations increased early in the morning and late in the evening. However, the concentrations of 2-NF and 2-NTP were low during the daytime and high at night. The opposite diurnal variability of 2-NF and 2-NTP compared with the diurnal variability of the primary emitted chemicals clearly indicates that 2-NF and 2-NTP did not originate from the primary combustion sources, but were formed by the atmospheric nitration of the parent FLRA and TP, respectively. 2-NF was found to be produced from the gas-phase reactions initiated by NO3 or OH radicals in the presence of NOx (Atkinson and Arey, 1994; Atkinson et al., 1990; Arey et al., 1986). At night, the atmospheric concentration of OH radicals, which are produced from photochemi-cal processes, is reduced almost to zero. On the contrary, NO3 radicals generally increase after sunset, and play a significant role in the atmospheric nighttime reactions. The nighttime increase in the 2-NF concentration observed in this study suggests the significance of the gas-phase NO3 radical-initiated nitration of FLRA. The increase in 2-NF during the nighttime could also be partly attributed to the transportation of the air mass containing 2-NF secondarily produced from the OH radical-initiated reaction of FLRA during the daytime. However, the concentration of 2-NP, which is probably not formed by an NO3 radical-initiated reaction but by an OH radical-initiated reaction (Atkinson and Arey, 1994) in the gas-phase, did not increase during the nighttime. This supports the idea that a significant part of 2-NF was produced by the reaction of FLRA with NO3 radicals in the gas phase, at least over the duration of the sampling in this study. 2-NTP was previously reported to be formed by a gassolid phase heterogeneous reaction (Yang et al., 2013; Ishii et al., 2000) or a gas-phase homogeneous reaction (Kameda et al., 2006) of the parent TP. Although both reactions, namely, the reaction of the TP deposited on a solid-surface with NO3/NO2/N2O5 and that of the gas-phase TP with OH radicals in the presence of NO2, yield 2-NTP, these processes can also yield abundant amounts of 1-NTP (Yang et al., 2013; Zimmermann et al., 2012; Kameda et al., 2006; Ishii et al., 2000). However, the gas-phase reaction of TP with NO3/NO2/ N2O5 produces almost only 2-NTP (Kameda et al., 2006). Therefore, the observed diurnal variation in 2-NTP in this study, which was similar to that of 2-NF and different from that of 1-NTP, strongly suggests that a significant part of 2-NTP in airborne particles collected during the sampling period was formed from the gas-phase NO3 radical-initiated reaction of TP in the atmosphere. We have previously demonstrated that the correlation between the atmospheric concentrations of 2-NTP and 2-NF (r=0.70, significance level p< 0.001) was significantly better than the correlation between 2-NTP and 2-NP (r=0.38, p<0.001) (Kameda et al., 2005). These correlation coefficients were based on more than 90 data sets. This result also supports the view that NO3 chemistry can yield atmospheric 2-NTP.

Table 2. 
Concentrations of selected inorganic gases and nitro-PAHs in 3-hr averaged samples of the airborne particles collected in Osaka, Japan on September 4-5, 2001 and November 28-29, 2001.
Date Timea
( JST)
Nitro-PAHsb Inorganic gases
1-NP 2-NP 2-NF 1-NTP 2-NTP COc NOxd
4-5, 2001
12:00 17 4 26 N.A. 9 0.3 37
15:00 22 18 11 N.A. 13 0.3 54
18:00 43 35 108 N.A. 16 0.6 47
21:00 34 52 187 N.A. 16 0.7 44
0:00 33 27 369 N.A. 31 0.6 48
3:00 28 17 293 N.A. 31 0.5 44
6:00 54 N.A. 553 N.A. 36 0.7 66
9:00 17 3 176 N.A. 22 0.4 32
12:00 40 1 63 N.A. 17 0.3 28
Mean 32 20 199 N.A. 21 0.5 45
28-29, 2001
12:00 87 N.A. 33 N.A. 10 0.6 13
15:00 29 21 64 22 16 0.7 22
18:00 82 86 168 72 23 1.1 46
21:00 96 61 272 32 31 1.3 53
0:00 41 49 412 12 43 1.0 35
3:00 37 34 313 8 26 0.8 20
6:00 59 76 239 12 27 1.1 35
9:00 47 26 81 8 20 0.8 17
12:00 43 52 201 33 20 0.9 43
Mean 58 51 198 25 24 0.9 32
Abbreviations of compounds: see text and Table 1.
NA: not available
aStart of sample collection
bGiven in unit of fmol m-3
cGiven in unit of ppmv
dGiven in unit of ppbv

Fig. 1. 
Diurnal variations in the concentrations of 1-NP (solid triangle), NOx (cross), and CO (open diamond) (a), and 1-NTP (solid diamond), 2-NTP (open square), 2-NF (open circle), and 2-NP (plus) (b) in south Osaka, Japan on November 28-29, 2001.

Changes in the concentrations of 1-NTP were accompanied by similar changes in the concentration of 2-NP (Fig. 1b). When the concentration of 2-NP increased, the increase was probably because of only the OH chemistry. Therefore, atmospheric 1-NTP was assumed to be formed mainly by an OH radical-initiated reaction; however, some part of it may have come from direct emissions from combustion processes.

The diurnal changes in the nitro-PAH concentrations in airborne particles collected on September 4-5 (abbreviated as Sept 4-5) (Fig. 2) and Nov 28-29 (Fig. 1) were similar, i.e., the concentrations of 1-NP and 2-NP were low in both daytime and nighttime, whereas those of 2-NF and 2-NTP were elevated in the nighttime. The 1-NTP concentration could not be determined during for the Sept 4-5 period owing to the lack of the sample amount.

Fig. 2. 
Diurnal variations in the concentrations of 1-NP (solid triangle), 2-NP (plus), 2-NTP (open square), and 2-NF (open circle) in south Osaka, Japan on September 4-5, 2001.

When all the data obtained on Sept 4-5 and Nov 28- 29 were combined, the 2-NF concentration increased linearly with an increase in the 2-NTP concentration (r=0.91, p<0.001), although the x-intercept value was significant (Fig. 3a). When the daytime (6:00- 15:00) and nighttime (18:00-3:00) data were plotted separately, the x-intercept was significant in the daytime (Fig. 3b), but almost zero in night (Fig. 3c). This result implies that the potential sources of 2-NTP, for example, direct emissions, existed during the daytime and that the nighttime formation pathways of 2-NTP and 2-NF were the same or almost similar. The mean value of the observed concentration ratio of [2-NF]obs/ [2-NTP]obs during the nighttime determined by a leastsquare analysis was 10.1. The rate of the atmospheric concentration change of 2-NF and 2-NTP can be given by the following equations based on their rate of formation by the NO3 radical-initiated reaction:

Fig. 3. 
Relations between atmospheric concentrations of 2-NF and 2-NTP in south Osaka, Japan measured September 4-5 and November 28-29, 2001. (a) All data; (b) daytime data (6:00- 15:00) only; (c) nighttime data (18:00-3:00) only.


where y2NF and y2NTP are, respectively, the yields of 2-NF and 2-NTP from the gas-phase reactions of FLRA and TP with NO3 radicals; kFLRA-NO3 and kTP-NO3 are the rate constants of the reactions; kloss-2NF and kloss-2NTP are, respectively, the rate constants for the atmospheric loss processes of 2-NF and 2-NTP such as photolysis and oxidation; and [FLRA] and [TP] are the gas-phase concentrations of FLRA and TP, respectively. Under steady state conditions, both these rates are equal to zero. Therefore, the ratio of the loss rate constant kloss-2NTP/kloss-2NF can be expressed as follows:


where [2-NF]ss and [2-NTP]ss are the steady state concentrations of 2-NF and 2-NTP, respectively. The concentrations of particle-associated FLRA and TP at the sampling site were reported to be comparable (Kameda et al., 2004). Significantly less literature is currently available on the gas-particle distribution of TP. Lammel et al. (2010a, 2010b) reported the particle-phase mass fractions of TP (θTP) and FLRA (θFLRA) to be 0.52-0.63 and 0.07-0.12, respectively, at ambient temperatures of 289.4-309.0 K. Therefore, assuming that the particlephase concentrations of TP and FLRA were the same, the gas-phase concentration ratio [TP]/[FLRA] was estimated to be ~0.08 using the mean θTP and θFLRA values. The reaction rate constant kFLRA-NO3 was determined to be 5.1×10-28[NO2] cm3 molecule-1 sec-1 and y2NF was determined to be 24% (Atkinson and Arey, 1994). Although the reaction rate constant kTP-NO3 was determined to be 0.66×10-28[NO2] cm3 molecule-1 sec-1 (Kameda et al., 2013), the yield of 2-NTP from the gasphase NO3 radical-initiated reaction has not been obtained. The relative loss rate kloss-2NTP/kloss-2NF was estimated to be ~0.1 based on the ambient concentrations of TP, FLRA, 2-NTP, and 2-NF, the rate constant for the reaction of TP with OH radicals, and the rate constant for the reaction of FLRA with OH radicals assuming the steady state condition as well as Eq (3) (Kameda et al., 2013). Therefore, using the reported reaction rate constants and assuming that [2-NF]ss/[2-NTP]ss=10.1, kloss-2NTP/kloss-2-NF=0.1, and [TP]/[FLRA]=0.08, Eq (3) gives the yield y2NTP of 23%. The yield of 2-NTP from the reaction of TP with NO3/NO2/N2O5 in CCl4 was determined to be 35% (Kameda et al., 2006). The nitro-isomer profiles of the reactions of several PAHs with NO3/NO2/N2O5 in CCl4 were similar to those in the gas-phase NO3 radical-initiated reactions (Phousongphouang and Arey, 2003; Zielinska et al., 1986). In those studies, the yield was higher than 20% for several types of nitro-PAH isomers in the gas-phase NO3 radical- initiated nitration, which is in agreement with our estimation of the yield of 2-NTP. The abundance of 2-NTP in the atmosphere, in spite of the low reactivity of the parent TP (Kameda et al., 2013; Nielsen, 1984), may be attributed not only to the high stability of 2-NTP (i.e. the small kloss-2NTP value) but also to the high yield of 2-NTP from the gas-phase NO3 radical-initiated reaction of TP.


In this study, diurnal concentrations of NTPs in airborne particles at a location in South Osaka, Japan were monitored at 3-hr intervals over two 27-hr periods. The concentration change in 1-NTP was very similar to that of 2-NP produced by an atmospheric OH radical-initiated reaction. On the contrary, the variations in the concentrations of 2-NF and 2-NTP were significantly different from those of other nitro-PAHs, i.e., they increased during the nighttime, suggesting that 2-NF and 2-NTP were formed via the NO3 radical- initiated nitration of the parent FLRA and TP in the atmosphere. Based on the ambient concentration of 2-NTP and the reported rate constant for the reaction of TP with NO3 radicals, the yield of 2-NTP from the gas-phase NO3 radical-initiated reaction of TP was newly determined to be 23%. This high yield may be one of the reasons for the high concentration of 2-NTP in the atmosphere. Although the observation period in this study was not recent, the results obtained in this study on the secondary formation of NTPs via the radical- initiated reactions can be considered to be general and independent of the observation year. Despite the strong mutagenicity of 2-NTP, very few studies have been performed to measure its concentration in the atmosphere. Although, in this study, we successfully estimated one of the factors that led to the high concentration of 2-NTP, further elucidation of the atmospheric behavior including the occurrence and loss processes of NTPs is desired.


We thank Prof. Koji Inazu of Numazu National College of Technology for helpful discussion throughout this work.

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