Enhanced secondary organic aerosol formation from the photo-oxidation of mixed anthropogenic volatile organic compounds
- 1State Key Laboratory of Environmental Criteria and Risk Assessment, Chinese Research Academy of Environmental Sciences, Beijing 100012, China
- 2Laboratory of Atmospheric Chemistry, Paul Scherrer Institute, 5232 Villigen, Switzerland
- 3State Key Laboratory for Structural Chemistry of Unstable and Stable Species, Beijing National Laboratory for Molecular Sciences, CAS Research/Education Center for Excellence in Molecular Sciences, Institute of Chemistry, Chinese Academy of Sciences, Beijing 100190, China
- 4Beijing Advanced Innovation Center for Soft Matter Science and Engineering, Beijing University of Chemical Technology, Beijing 100029, China
Correspondence: Hong Li (email@example.com)
Vehicular exhaust is one of the important contribution sources of secondary organic aerosol (SOA) in urban areas. Long-chain alkanes and aromatic hydrocarbons are included in gaseous organic pollutants of vehicle emissions, representative of diesel and gasoline vehicles respectively. In this work, the SOA production from individual anthropogenic volatile organic compounds (AVOCs) (n-dodecane, 1,3,5-trimethylbenzene) and mixed AVOCs (n-dodecane + 1,3,5-trimethylbenzene) was studied with a large-scale outdoor smog chamber. Results showed that the SOA formation from the mixed AVOCs was enhanced compared to the predicted SOA mass concentration based on the SOA yield of individual AVOCs. According to the results of mass spectrometry analysis with electrospray ionization time-of-flight mass spectrometry (ESI-ToF-MS), interaction occurred between intermediate products from the two precursors, which could be the main reason for the enhanced SOA production from the mixed AVOC reaction system. The study results could improve our understanding about the contribution of representative precursors from vehicular exhaust to the formation of SOA in urban areas. This study also indicates that further studies on SOA chemistry from the mixed VOC reaction system are needed, as the interactions between them and the effect on SOA formation can give us a further understanding of the SOA formed in the atmosphere.
Secondary organic aerosol (SOA) has received considerable attention during the past few decades, as it plays an important role in affecting global climate change (Shrivastava et al., 2017; von Schneidemesser et al., 2015; Mellouki et al., 2015; Kanakidou et al., 2005), atmospheric visibility (R. Zhang et al., 2015; Moise et al., 2015; Laskin et al., 2015; Ren et al., 2018), and public health (Poschl, 2005; Poschl and Shiraiwa, 2015; Zhang et al., 2016; Requia et al., 2018). The formation, growth, and transformation of SOA influence the atmospheric aerosol's physicochemical properties (Poschl and Shiraiwa, 2015; Moise et al., 2015; Mellouki et al., 2015; Herrmann et al., 2015). The precursors of SOA mainly include anthropogenic volatile organic compounds (AVOCs) and biogenic volatile organic compounds (BVOCs) (Kelly et al., 2018); in urban areas, AVOCs are the main sources of SOA, e.g., gasoline vehicle emissions (Johnson et al., 2004; Charron et al., 2019; Yang et al., 2018), diesel vehicle emissions (Paulsen et al., 2005; Wirtz and Martin-Reviejo, 2003; Odum et al., 1996; Zhao et al., 2015), and solvent use (Li et al., 2017c; Kansal, 2009).
Early regional air quality models underestimated the observed SOA concentrations in large areas of the atmosphere (Volkamer et al., 2006; Heald et al., 2005; de Gouw et al., 2005; Appel et al., 2017; J. Huang et al., 2017); since incorporating the newly discovered SOA sources, the gap between the observed and predicted SOA concentrations has been decreasing (Zhao et al., 2016; Slowik et al., 2010; Hodzic et al., 2010). The SOA formation processes in the atmosphere are very complicated; although the degradation of most VOCs is clear now, the formation and aging of a large amount of SOA is still unclear. Previous studies found that the observed organic aerosol concentration could not be explained by the traditional yields of the measured AVOCs (de Gouw et al., 2005); in addition, field observations found that potential interactions between AVOCs and BVOCs existed during SOA formation (Spracklen et al., 2011; Hoyle et al., 2011; Glasius et al., 2011; Galloway et al., 2011; Kari et al., 2019): AVOCs could enhance (Spracklen et al., 2011; Carlton et al., 2010; Shilling et al., 2013) or suppress SOA formation from BVOCs (Kari et al., 2019). A recent study also found that SOA formation could be reduced by the mixture of BVOCs (McFiggans et al., 2019). These findings indicate that there are interactions in the complex mixtures of VOCs which may influence the SOA production estimation if they are considered in models.
In urban areas, vehicular exhaust is one of the important sources of SOA, the representative substances of which include aromatic hydrocarbons and long-chain alkanes (Paulsen et al., 2005; Wirtz and Martin-Reviejo, 2003; Charron et al., 2019; Saathoff et al., 2009; Zhao et al., 2015; Gentner et al., 2012). As an important contributor to SOA in urban areas, aromatic hydrocarbons are generally concerned about their kinetics (Atkinson and Arey, 2003; Calvert et al., 2002), reaction mechanisms (Tsiligiannis et al., 2019; Midey et al., 2003; M. Huang et al., 2017b; Wang et al., 2020; Garmash et al., 2019), SOA yield (Cao and Jang, 2007; Kroll et al., 2007; Ng et al., 2007b; M. Huang et al., 2017a), ozone generation potential (Luo et al., 2019), and SOA physicochemical properties (optical properties, morphology, etc.) (Grosjean, 1981; K. Li et al., 2018, 2017; Phillips and Smith, 2014; Kim and Paulson, 2013; Huang et al., 2018). Long-chain alkanes, as representative substances of intermediate volatile organic compounds (IVOCs), are considered a potential contributor of SOA (Robinson et al., 2007; Trostl et al., 2016; Shiraiwa et al., 2013). Studies about long-chain alkanes include SOA chemical composition (Fahnestock et al., 2015; Yee et al., 2013; Aimanant and Ziemann, 2013; Yee et al., 2012), SOA yield (Loza et al., 2014; Tkacik et al., 2012), and SOA optical properties (J. Li et al., 2017a, 2020). Aromatic hydrocarbons and long-chain alkanes are generally studied separately in the laboratory. However, it should be noted that in the real atmosphere, aromatic hydrocarbons and long-chain alkanes often exist at the same time, especially from vehicle emissions (Wu and Xie, 2018). The studies that cover these two types of substances in one reaction system are still limited, and the corresponding SOA formation and reaction processes are not yet clear.
In this work, 1,3,5-trimethylbenzene and n-dodecane are selected as representative substances. As the concentration of 1,3,5-TMB is much higher than that of n-dodecane in both the gasoline compositions and ambient air, the initial concentration ratio of 1,3,5-TMB and n-dodecane in this work is about 10:1 (ppbv). Schauer et al. (2002) reported that 1,3,5-TMB and n-dodecane in the gasoline composition were about 7450 and 136 µg g−1, respectively; Gentner et al. (2012) reported that the weight percentages of 1,3,5-TMB and n-dodecane in liquid gasoline were 0.530–0.881 and 0.004–0.045 (% weight by carbon), respectively. According to field observations in China, the measured 1,3,5-TMB concentration at the rural site in the YelRD (Yellow River Delta) region in 2017 could reach 1.447 ppb (Chen et al., 2020), and the measured C12 alkane concentration was 0.122±0.12 ppb in the PRD (Pearl River Delta) region and 0.129±0.086 ppb in the NCP (North China Plain) region in 2018 (Wang et al., 2020).
This work aims to investigate the SOA formation from the mixed AVOC reaction system. In this study, the SOA yield derived from n-dodecane and 1,3,5-trimethylbenzene in the presence of HONO was obtained in a large-scale outdoor smog chamber, and the SOA derived from the mixed AVOCs was measured. The measured SOA mass concentration from the mixed AVOC reaction system was compared to the predicted SOA mass based on the SOA yield of n-dodecane and 1,3,5-trimethylbenzene. SOA particles were collected and analyzed with electrospray ionization time-of-flight mass spectrometry (ESI-ToF-MS) to achieve insight into the chemical composition and interactions. The results here are helpful to improve our understanding of the contribution of representative precursors from vehicle exhaust to SOA.
2.1 Experimental methods
The experiments were conducted in a 56 m3 (3.2 m × 6.2 m × 2.5 m) outdoor smog chamber constructed at the Chinese Research Academy of Environmental Sciences (the CRAES chamber; 40∘02′27.73′′ N, 116∘24′41.56′′ E). Details of the chamber have been described previously (Li et al., 2021). Briefly, the chamber was made of FEP Teflon film, the light transmission of which was above 90 % at the wavelength of 350–900 nm. The substances inside the chamber could be mixed well within 4 min. The experimental duration under solar irradiation was about 7–8 h. After each experiment, the chamber was cleaned with zero air for at least 24 h with a flow rate of 200 L min−1.
1,3,5-trimethylbenzene or n-dodecane was introduced into the chamber by zero air through the custom-made U-shaped glass tube with a known volume of liquid 1,3,5-trimethylbenzene or n-dodecane. Concentrations of 1,3,5-trimethylbenzene and n-dodecane were measured before and after reactions by collecting samples on Tenax TA solid adsorbent and analyzing by thermal desorption–gas chromatography with flame ionization detection (TD, UNITY-xr; GC, 7890B). The OH precursor of the experiments was HONO; it was prepared by dropwise addition of 1 mL 2 wt % NaNO2 solution into 2 mL 15 wt % sulfuric acid solution in a custom-made glass bubbler, the bubbler was attached to the smog chamber with a Teflon tube, and the formed HONO was introduced into the chamber by zero air. The NO and NO2 and formed ozone in the chamber were measured by an NOx analyzer (EC9841, ECOTECH, Australia) and an ozone analyzer (EC9830, ECOTECH, Australia), respectively. After the gas species mixed evenly in the chamber, the enclosure of the chamber was opened.
After each photochemical experiment, the formed aerosol particles in the chamber were collected by a low-flow sampler (LV 40BW, Sibata Scientific Technology Ltd., Soka, Japan) at a flow rate of 5 L min−1 for 10 min. The PTFE filters (0.2 µm, 47 mm, Merck Millipore, type FGLP) used were extracted in 5 mL methanol sonicating for 30 min. The methanol solutions were analyzed with ESI-TOF-MS (Bruker, Impact II) in positive mode, and the chemical compositions of the formed SOA were obtained. The methanol solutions were also detected with a UV–Vis light spectrometer (Hitachi, U-3900), which was used to detect the absorbing property of the formed SOA. The attenuated total internal reflection infrared (ATR-IR) analysis was applied to determine the potential functional groups in SOA extracts; an FTIR spectrometer (Bruker, Tensor 27) equipped with a RT-DLaTGs detector was used. The SOA extracts were deposited and dried directly on the Diamant crystal of an ATR-IR cell. The spectra of the dry SOA extracts were recorded using a background spectrum obtained with no samples as the reference (100 scans, 2.4 cm−1 resolution).
The following chemicals were used without further purification: 1,3,5-trimethylbenzene (1,3,5-TMB) (99 %, Acros), n-dodecane (>99 %, Alfa Aesar), sulfuric acid (>95 %, Beijing Chemical Works), sodium nitrite (98 %, Alfa Aesar), methanol (99.9 %, Merck), and acetonitrile (99.8 %, Fisher Chemical).
2.2 Calculation methods
2.2.1 Wall-loss corrections
As SOA yields could be underestimated due to the losses of SOA forming vapors to chamber walls, the vapor wall loss was considered and corrected in this work (Zhang et al., 2014). The competition between the uptake of organic vapor by the chamber walls and the aerosol particles would determine the effect of vapor wall loss on SOA yields (X. Zhang et al., 2015). The ratio of average gas–particle partitioning timescale () to the vapor wall-loss timescale () could be used to evaluate the underestimation of SOA yields (Zhou et al., 2011; Chen et al., 2019).
The average gas–particle partitioning timescale () could be expressed as the following equation (Seinfeld and Pandis, 2016; Zhang et al., 2014):
where was the average number concentration of the formed particles during the experiment, was the number mean diameter of the particles, Dgas was the gas-phase diffusivity, and was the Fuchs–Sutugin correction for noncontinuum mass transfer (Seinfeld and Pandis, 2016).
The vapor wall-loss timescale () could be expressed as the following equation (X. Zhang et al., 2015):
where kw was the wall loss rates of the organic vapor; was the ratio of surface to volume of the chamber, 1.55 m−1 for this chamber; aw was the mass accommodation coefficient of vapors deposition to the wall (10−5 was used here) (Zhang et al., 2014); was the root mean square speed of the gas; and ke was the eddy diffusion coefficient, which was set to 0.12 s−1 according to the reported values for a 60 m3 chamber (McMurry and Grosjean, 1985). Detailed calculation of , Dgas, kn, and is shown in the Supplement. The uncertainty of the mass correction here is about ±11.2 % (see Supplement for details).
Particle wall loss to chamber walls would also cause underestimation when calculating the SOA yield from measurements if these losses were not corrected for. Thus particle wall loss was accounted for during the experiments. The particle growth data were corrected for wall loss, in which size-dependent coefficients from inert particle wall-loss experiments (ammonium sulfate) were applied to the particle volume data (Li et al., 2021):
where kdep(d) was the wall-loss coefficient of particles in the diameter d.
2.2.2 SOA yields
The secondary organic aerosol (SOA) yield (Y) was defined as the fraction of a reactive organic gas (ROG) that was converted to aerosols, and it could be calculated by the following equation:
where ΔMo (µg m−3) was the mass concentration of the organic aerosol, and ΔROG (µg m−3) was the amount of the ROG reacted.
For the mixed anthropogenic volatile organic compounds (AVOCs), the formed SOA mass was predicted based on the SOA precursors and their SOA yield measured in this study. The possible nonlinear interactions between the anthropogenic VOC mixtures were not taken into account. Specifically, the calculation equation (Kari et al., 2019) could be expressed as follows:
where ΔROGi was the amount of the ROGi reacted, and Yi was the SOA yield of ROGi.
a The mass here is the measured value with the SMPS; the density of the
formed SOA derived from 1,3,5-TMB is assumed to be 1.4 g cm−3 (Zhang et
al., 2016; Nakao et al., 2013); the density of the formed SOA derived from
is assumed to be 1.06 g cm−3 (Lim and Ziemann, 2009; J. Li et al., 2017); the density of the formed SOA derived from the mixed AVOCs is assumed to be 1.23 g cm−3. b The predicted mass here is based on the yield that the particle and
vapor wall loss are not considered. c The corrected mass here is calculated after taking particle and vapor wall loss into account. d The predicted mass here is based on the yield that the particle and vapor wall loss are considered. e The
SOA yield here is calculated after taking particle and vapor wall loss into account.
A set of experiments are conducted in summer, of which the initial conditions and general results are shown in Table 1. The experiments are conducted as follows: n-dodecane + HONO; 1,3,5-trimethylbenzene + HONO; n-dodecane + 1,3,5-trimethylbenzene + HONO. The experiments are conducted under similar conditions, and the details of the relative humidity (RH), temperature (T), and the NO2 photolysis rate (J(NO2)) of the experiments are shown in Fig. S1. Ng et al. (2007a) reported that the efficient photolysis of HONO (the same method with this study) could generate relatively high concentrations of OH, 1 ppm NO molecules cm−3 OH initially. The NOx concentration applied in this work is in the range of 190–260 ppb, resulting in the estimated OH concentration being (4–5.2) × 106 molecules cm−3 in the pure and mixed experiments. The NO2 photolysis rates of the experiments at noon in summer are in the range of 0.005–0.006 s−1; for the experiment MIX-3, the weather is cloudy, and the J(NO2) at noon is relatively smaller, 0.004 s−1. The temperature in summer at noon is in the range of 30–46∘, and the RH inside the chamber is <10 %. The reaction profiles of photo-oxidation of n-dodecane, 1,3,5-TMB, and mixed AVOCs under HONO conditions in summer are shown in Fig. 1. According to a previous study (Chen et al., 2019), the formed inorganic nitrate is negligible for the high-NOx oxidation of gasoline, in which the experimental conditions are similar to this study (NOx 130 ppb, formed aerosol mass concentration 34.6 µg m−3). In the pure and mixed experiments, the NOx concentration is equivalent, so the formed nitric acid should be similar. Therefore, the increase in particle mass concentration in the mixed experiments is likely from the organic aerosols.
The SOA yields of n-dodecane and 1,3,5-TMB are 14.1 %–23.1 % and 1.1 %–2.4 %, respectively, as shown in Table 1. The predicated SOA mass derived from the mixture of these VOCs is based on the measured SOA yields of n-dodecane and 1,3,5-TMB, without considering possible nonlinear interactions between them. Then the observed SOA mass is compared to the predicted values. It can be seen that nearly all the measured values are higher than the predicted SOA mass both before and after wall-loss correction. In other words, the SOA formation is enhanced when the two AVOCs are mixed, indicating the potential synergistic effect may exist in the mixed AVOC reaction system. The findings above will be discussed further in the following sections.
3.1 Enhancement of SOA formation
Figure 1 shows the formation and evolution of the SOA during the photochemical reaction processes in summer. The number mean diameter, number concentration, surface mean diameter, total surface, and mass concentration of the particles are analyzed and compared. The number mean diameters of the formed particles from n-dodecane, 1,3,5-TMB, and the mixture are 100, 50–100, and 150–200 nm, respectively. This suggests that after mixing the two precursors, the number mean diameter of the formed particle became larger. The number concentration of the formed particles, similarly, increased from 2.0×103 cm−3 for single precursors to above 1.0×104 cm−3 for the mixture. Because of the enhanced particle number concentration and diameter, the mass concentration of particles increases from <4 µg m−3 for individual precursors to >40 µg m−3 for the mixture. It can be seen that the mass concentration of SOA generated by the mixed AVOC system is significantly higher than the sum of the SOA generated by the two separate systems. It should be noted that the surface mean diameter of the particles from n-dodecane, 1,3,5-TMB, and the mixed AVOCs is all around 200 nm. However, due to the enhanced number concentration for mixture, the total surface of the formed particles for the mixture ( nm2 cm−3) was higher than individual precursors ( nm2 cm−3 for n-dodecane; nm2 cm−3 for 1,3,5-TMB). Overall, after the two precursors are mixed, the number mean diameter, number concentration, total surface, and mass concentration of the generated particles were improved, while the surface mean diameter of the particles did not change.
From the results shown above, we know that the SOA yield is significantly enhanced when mixing n-dodecane and 1,3,5-TMB. Experimental conditions can influence the SOA yields; however, the effect is not obvious. First, precursor concentration may play a role; however, we can rule it out based on the analysis below. Several previous studies (Lauraguais et al., 2012; Loza et al., 2014; Zhou et al., 2011; Ng et al., 2007a) have reported that the aerosol formation is strongly affected by the initial precursor concentration, with a higher initial concentration of precursor leading to higher SOA yields. As higher initial precursor concentration will produce a higher amount of condensable products through chemical processes, the formed SOA mass will be higher. The aerosol present in the system will directly affect the gas–particle partitioning; as the medium, it can adsorb the oxidation products. Thus, higher SOA mass will lead to higher SOA yield (Lauraguais et al., 2014). In this work, for TMB-1 and TMB-2, while keeping the HONO concentration basically unchanged, the concentration of 1,3,5-TMB increases from 105 ppb (514.5 µg m−3) to 178 ppb (882.9 µg m−3); the yield increases by only 0.9 %. For the mixed AVOC reaction system, the concentrations of the precursors for MIX-1 and MIX-2 are 168 and 155 ppb (824.2 and 756.2 µg m−3, 1,3,5-TMB) and 28 and 22 ppb (194.7 and 152.3 µg m−3, n-dodecane), respectively. Compared with TMB-2 experiments, the concentration of MIX precursor is only increased by about 136 and 25.6 µg m−3 (3 %–15 %). According to the SOA yields of the TMB reaction system, the increase in the precursors mass concentration of the mixture system is not the reason for the large increase in the SOA mass concentration. Second, NOx may also influence the SOA yield, but that is likely not the case here. Tsiligiannis et al. (2019) observed that the particle formation strongly varied with NOx conditions, and the increasing ratio would suppress the SOA formation. In this work, regardless of whether it is a single or a mixed reaction system, the NOx concentration in the system remains basically unchanged. Experiments TMB-2, MIX-1, and MIX-2 have a similar ratio, all around ∼8, but the formed SOA mass concentration is quite different. This indicates that the ratio here has little effect on the enhanced SOA mass concentration of the mixed AVOC reaction system.
Rate constants for the reactions of n-dodecane and 1,3,5-TMB with the OH radical at 298 K are and cm3 molecule−1 s−1, respectively (Atkinson and Arey, 2003). As shown in Table S3, OH reactivity of Dod-1 and Dod-2 is about 6.5–7.1 s−1; OH reactivity of TMB-2 and TMB-3 is in the range of 237.1–248.3 s−1; and OH reactivity of MIX-1, MIX-2, MIX-3, and MIX-4 is in the range of 223.3–361.5 s−1. This indicates that OH reactivity of the mixed experiments differs greatly from that of dodecane experiments, but it is very close to that of 1,3,5-TMB experiments. However, the mixed experiments still have a large enhancement in SOA formation compared with 1,3,5-TMB experiments, indicating that this enhancement is likely not due to the different OH reactivity. Rate constants for the reactions of NO2 and NO with the OH radical at 298 K are and cm3 molecule−1 s−1, respectively (Atkinson et al., 2004). The OH reactivity of NOx is similar for all experiments (189.6–238.8 s−1) and therefore likely plays a minor role in influencing SOA concentration.
For the enhancement in SOA yield of the mixed AVOC system, we propose two possible conjectures, as revealed in Fig. 2. The first conjecture is that the gas–particle partitioning of the system has changed. The SOA yield of n-dodecane (14.1 %–23.1 %) is significantly higher than that of 1,3,5-TMB (1.1 %–2.4 %), so the volatility of its products (including gas phase and particle phase) is relatively lower, and it is easier to form particles, e.g., nucleation; for the 1,3,5-TMB reaction system, the products have higher volatility and are difficult to condense and nucleate, so the yield is lower. When 1,3,5-TMB is mixed with n-dodecane, the products of n-dodecane provide a lot of particles for the products of 1,3,5-TMB to condense, so the yield is greatly improved. Another conjecture is that there are chemical interactions between the two systems; i.e., the intermediate products of the two precursors may react with each other.
In order to know which conjecture is correct, different injection experiments are performed: n-dodecane and HONO are introduced into the chamber firstly, and after 1 h (Fig. 3c and d, MIX-6) or 4 h (Fig. 3a and b, MIX-7) of photochemical reaction, 1,3,5-TMB is introduced into the chamber. As shown in Fig. 3a and c, after the introduction of 1,3,5-TMB, the mass and number concentration of the particles have a certain increase, and the consumption of NOx is accelerated. However, compared with Fig. 3e (n-dodecane and 1,3,5-TMB are added together before the photochemical experiments, MIX-4), the final SOA mass concentrations of MIX-6 and MIX-7 (Fig. 3a and c) are much lower. If our first conjecture plays an important role, one would expect large SOA mass enhancement (similar with mixed experiments) as the products of n-dodecane provide enough condensational sink for 1,3,5-TMB products to condense. The result here indicates that the gas–particle partitioning conjecture plays a minor role in the SOA yield enhancement. To further verify our second conjecture, the particle compositions are analyzed and shown below.
Figure 4 shows the ESI-ToF-MS mass spectra of SOA generated from n-dodecane, 1,3,5-TMB, and mixed AVOCs. The representative identified products with strong intensity are shown in Fig. S2 and Table 2. The identified products are mainly based on the mass spectra and previous related studies (Tsiligiannis et al., 2019; J. Li et al., 2017; Sato et al., 2019). As shown in Fig. 4, most products from n-dodecane, 1,3,5-TMB, and mixed AVOC SOA are concentrated around 200–450; in the range of 500–700, oligomers are formed.
Huang et al. (2015) reported that the predominant products for the aging of 1,3,5-trimethylbenzene secondary organic aerosol were organic nitrogen-containing products, aromatic organic acid, oxocarboxylic acid, and oligomer compounds. Due to the various ratios, the formed products might be different. Usually, higher NO would lead to the suppression of oligomers and particle formation, and higher NO would increase the formation of organonitrates (Tsiligiannis et al., 2019). The products derived from n-dodecane in the presence of NOx were mainly oxygen-containing organic compounds (i.e., peroxyhemiacetals, hemiacetals, esters, aldol condensation) and organonitrate products (Fahnestock et al., 2015; Lim and Ziemann, 2005). As shown in Table 2, the products derived from 1,3,5-TMB are mainly organonitrates and oxygen-containing organic compounds. For products derived from n-dodecane, the main components are also oxygen-containing organic compounds and organic nitrates. It should be noted that in the mixed AVOC system, some products are not detected in the separate reaction system (n-dodecane or 1,3,5-TMB), such as C16H30O4, C16H24O5, C29H48O10, and C35H68O10. This indicates that interactions occur between the intermediate products from n-dodecane and 1,3,5-TMB.
The gas-phase products of OH-initiated oxidation of 1,3,5-TMB in the presence of NOx are mainly 3,5-dimethyl benzaldehyde (C9H10O), 3,5-dimethylbenzoic acid (C9H10O2), 2-methyl-4-oxo-2-pentenal (C6H8O2), 2-methyl-4-oxo-2-pentenoic acid (C6H8O3), 2,4,6-trimethylphenol (C9H12O), and 3,5-dimethyl-2-furanone (C6H8O2) (Huang et al., 2015), which contain carbonyl or hydroxyl groups that are formed within 1h photochemical reaction. The intermediate products of OH-initiated oxidation of n-dodecane in the presence of NOx are also compounds containing carbonyl and hydroxyl groups, and more alcohol can be formed due to the RO2+NO reaction compared to the low-NOx condition (Fahnestock et al., 2015). These compounds tend to undergo an acetal reaction and/or esterification reaction in the particle phase. When the photochemical reaction is initiated, the intermediate products produced by 1,3,5-TMB and n-dodecane exist in the same reaction system, and acetal and esterification reactions are more likely to occur in the particle phase due to higher concentration of aldehydes, ketones, alcohols, and carboxylic acids. The proposed reaction mechanism of the mixed AVOC system is shown in Fig. 5. As an example, C16H24O5, which has a much higher intensity in the mixed AVOC system (as shown in Table 2 and discussed above), might be an ester from the reaction of an acid and an alcohol from 1,3,5-TMB and n-dodecane, respectively.
3.2 Light absorption of secondary organic aerosol
Figure 6a shows the UV–Vis spectra of the n-dodecane, 1,3,5-TMB, and mixed AVOC SOA filter extract. Before analyzing the samples, the blank PTFE membrane filter is dissolved with methanol, and the ultraviolet–visible absorption spectrum of the methanol solution is analyzed. The absorption of the SOA filter solutions is mainly concentrated in the wavelength of <300 nm. This is consistent with previous literature reports: J. Li et al. (2017) found that the n-dodecane SOA solutions had no detectable absorption in the wavelength of >350 nm; Huang et al. (2018) found that the 1,3,5-TMB SOA solutions also had no obvious absorption in the wavelength of >300 nm. Based on the light absorption spectra, the mass absorption efficiency (MAE; m2 g−1) of the SOA in the extracts is calculated using the following equation (Chen et al., 2016):
where Abs(λ) is the light absorption coefficient (m−1), and COM is the SOA mass concentrations in the extracts. The MAE of the SOA extracts in Fig. 6a was calculated from 200 to 300 nm. The MAE values at 205 nm were in the following order: 1,3,5-TMB SOA (56.8 m2 g−1) > dodecane SOA (42.5 m2 g−1) > mixed AVOC SOA (19.5 m2 g−1). The MAE in the 210–250 nm band also shows the same pattern. This indicates that the SOA generated by the mixed AVOCs contains less light-absorbing substance per unit mass relative to dodecane SOA and 1,3,5-TMB SOA.
To further determine the potential functional groups in SOA extracts, ATR-IR spectra were acquired (Fig. 6b). To eliminate the influence of water, experiments were conducted under dry conditions. As shown in Fig. 6b and Table S4, the bold peak at 3360 cm−1 corresponds to the characteristic peak of C–OH in alcohol. The peak at 3192 cm−1 originates from the O–H stretching vibration of carboxylic acid. The two characteristic peaks at 2921 and 2850 cm−1 correspond to the C–H stretching vibration of alkane. The peaks at 1660 and 1633 cm−1 originate from C=O stretching vibrations. The signals at 1465 and 1415 cm−1 represent the deformation vibrations of methyl and methylene groups. The peak around 1268 cm−1 corresponds to the vibration of nitrate groups in nitrate ester. The results above suggest that the SOA extracts are dominantly composed of carbonyl compounds, carboxylic acid, nitrate ester, and alcohol. This is consistent with previous studies (Huang et al., 2015; Fahnestock et al., 2015).
3.3 Factors affecting the formation of SOA and ozone
According to previous studies, ozone concentration was statistically positively correlated with temperature, solar radiation intensity, and sunshine hours and was negatively correlated with precipitation, relative humidity (RH), visibility, and wind speed (Wang et al., 2017; Huang et al., 2019; Jaffe and Zhang, 2017). The factors affecting ozone generation included solar radiation intensity, temperature, and precursor concentrations. Figure 7 shows the generation of ozone during the photochemical reactions of three different reaction systems. As shown in Fig. 7a, for the n-dodecane reaction system, the ozone concentration was Dod-1 > Dod-2. As revealed by Table S2 and Fig. S1, under a similar ratio and solar radiation intensity (J(NO2)), the higher temperature would promote the formation of ozone. For the 1,3,5-TMB reaction system, the formed ozone concentration was in the following order: TMB-2 > TMB-3 > TMB-1. The corresponding ratio was 8.13, 6.12, and 4.48, respectively. The temperature conditions were TMB-1 > TMB-2 > TMB-3. The J(NO2) was similar for the three experiments. With similar solar radiation intensity, the ratio of precursors played a decisive role in the generation of ozone concentration compared to the temperature conditions. For the mixed AVOC reaction system, the order of formed ozone concentration was MIX-2 > MIX-1. The corresponding ratio was 7.83 and 8; the J(NO2) was MIX-1 ∼ MIX-2. The TMB/Dod ratio was 7 and 6. This indicated that, under a similar ratio and J(NO2) conditions, a higher ratio would promote the formation of ozone. For experiments MIX-2 and MIX-3, the ratios were similar, the temperature conditions were MIX-2 > MIX-3, and the J(NO2) was MIX-2 ∼ MIX-3, and the ratios were 9.1 and 7. The conditions above indicated that the higher ratio played a decisive role in the generation of ozone concentration. Higher temperature and a higher () ratio in a separate reaction system will promote the generation of ozone; the relative content of reaction precursors () in the mixture system will affect the concentration of ozone. With a similar ratio, a higher concentration of 1,3,5-TMB will promote ozone generation.
As shown in Fig. 8, for the n-dodecane reaction system, the mass concentration, number concentration, and total surface of the particles were Dod-1 < Dod-2. According to Fig. S1 and Table S2, under a similar ratio and J(NO2), the lower temperature would promote the formation of particles. However, the surface mean and number mean diameter of the two experiments were around 100 and 200 nm; this indicated that temperature had little effect on the diameter of the formed particles. For the 1.3.5-TMB reaction system, under similar J(NO2), lower temperature and a higher ratio would promote the particle formation; temperature and the ratio had little effect on the particle diameters. For the mixed experiments, under a similar ratio, compared with J(NO2) and temperature, a higher ratio would promote particle formation; similarly, the above conditions had little effect on the particle size. Lower temperature and a higher () ratio in a separate reaction system will promote particle formation; the relative content of reaction precursors () in the mixture system will affect the formed particles. With a similar ratio, a higher concentration of n-dodecane would promote the generation of particles; reaction conditions have little effect on the size of the final particle size.
Our findings demonstrate that the SOA yield derived from the mixed anthropogenic volatile organic compounds (n-dodecane + 1,3,5-TMB) in the presence of HONO is higher than the predicted value. The results of this work further demonstrate the inaccuracy of the SOA yield calculation method for the VOCs mixture, i.e., the simple linear addition of SOA yields from the individual yield of the compound in the VOC mixture. This calculation method may underestimate or overestimate the SOA production. In this work, the SOA production from the mixed n-dodecane and 1,3,5-TMB is underestimated. In the general case, the SOA yields from the individual compounds should be used with caution when calculating the SOA yields from the VOC mixture. In addition, as the representative substances of motor-vehicle exhaust, long-chain alkanes and aromatic hydrocarbons exist in the atmosphere at the same time. The increase in SOA yield after mixing the two kinds of compounds gives us an insight into the SOA yield derived from vehicular exhaust. Our results indicate that SOA formation needs to be considered more realistically in the atmosphere.
In summary, a set of photochemical experiments are carried out in a large-scale outdoor smog chamber. The measured SOA mass concentration of the mixed AVOCs (n-dodecane + 1,3,5-TMB) is compared to the predicted SOA mass concentration based on the SOA mass yields of the individual compounds. Results show that the SOA formation from the mixed AVOCs is enhanced. Mass spectra of the SOA particles indicate that interaction occurs between the intermediate products from the two precursors, and the products previously present in the gas phase may enter the particle phase through this inter-reaction. This could be the main reason for the enhanced SOA production from the mixed AVOC reaction system. The SOA formation and the ozone formation vary with the ratio, the temperature, and the solar radiation intensity.
Further research is needed to study the SOA chemistry from biogenic–biogenic VOC mixtures, biogenic–anthropogenic VOC mixtures, and anthropogenic–anthropogenic VOC mixtures. The interactions between VOC mixtures and the effect on SOA formation need to be determined.
The data used in this study are available upon request from the corresponding author.
The supplement related to this article is available online at: https://doi.org/10.5194/acp-21-7773-2021-supplement.
JL and HL conceived and led the studies. JL, KL, YC, HZ, XZ, and ZW performed chamber simulation and data analysis. HL, YL, XW, WW, and MG discussed the results and commented on the paper. JL prepared the article with contributions from all co-authors.
The authors declare that they have no conflict of interest.
We would like to thank Bin Liang from Bruker for supporting us with the mass spectrometry analysis.
This research has been supported by the Beijing Municipal Science & Technology Commission (grant no. Z181100005418015), the China Postdoctoral Science Foundation (grant no. 2019M660752), and LAC/CMA (grant no. 2019B08).
This paper was edited by Roya Bahreini and reviewed by two anonymous referees.
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