Seasonal Variation Characteristics of VOCs and Their Inﬂuences on Secondary Pollutants in Yibin, Southwest China

: Volatile organic compounds (VOCs) have a crucial impact on the formation of ozone and secondary organic aerosols in the near-surface atmosphere. Understanding the composition characteristics and sources of VOCs is necessary for determining effective control policies to mitigate VOCs and related secondary pollutions. We performed on-line measurements of VOC species in typical months of each season in Yibin, a fast-growing city in Sichuan Basin in China, to identify VOC seasonal characteristics, sources, and the potential for secondary pollution formation. The average mixing ratio of VOCs in Yibin was 22.3 ppbv. Five major emission sources were identiﬁed through the positive matrix factorization model, namely, gasoline vehicle, diesel vehicle, industrial manufacturing, solvent utilization, regional background, and secondary formation. Aromatics and alkenes played leading roles in the secondary formation of ozone and secondary organic aerosols. Furthermore, m/p-xylene, ethylene, and toluene were identiﬁed to be the major reactive species. Future management should consider targeting these compounds when evaluating ozone and aerosol reduction strategies. Vehicle and solvent utilization emission mitigation would be the primary and effective ways to improve air quality in the fast-developing city in this region.


Introduction
Volatile organic compounds (VOCs) are significant precursors to the formation of ozone and secondary organic aerosols (SOA) [1][2][3][4][5]. They contribute to the ability of atmospheric oxidation [6][7][8][9] and further impact the quality of air, thus threatening human health. Petrochemical or industrial facilities especially can spread out various VOCs, and some of them have been identified as a crucial factor to influence human health [10][11][12], including toluene, benzene, and 1,3-butadiene [13]. Due to rapid urbanization and industrialization, air pollution has been an urgent problem to handle [14,15]. In recent years, ground-level ozone (O 3 ) and haze events have heavily bothered urban cities in China due to the abundant emissions of precursors such as VOCs and NOx, the main factors forming photochemical pollution [16,17]. Thus, a better understanding of VOCs' sources and their impact on secondary pollutant is crucial for making effective emission control plans.
Trying to figure out VOC sources and pollution features will help to effectively control secondary pollutants, such as O 3 , SOA, and peroxyacetyl nitrate (PAN) [18]. Sun and his team found that urban pollution mainly originated from anthropogenic sources, which contained vehicular exhaust, vegetation emission, solvent usage, secondary formation, and biomass burning [19]. Tan studied the temporal and spatial distribution characteristics and source origins of VOCs in Chengdu, a typical city in Sichuan Basin, and gained two dominant VOC sources, which were motor vehicle exhaust and solvent utilization [20]. Research showed that in other cities of China, industrial emissions, automobile emissions, and biomass combustion emissions were considered to be the main sources of VOCs [21][22][23][24]. Except for them, the VOC reactivity was an essential factor for ambient VOCs to form secondary pollutants in large cities [25][26][27]. Different sources could spread out various characteristic VOC species; for example, propene was the dominant driver of internal combustion engines and was identified as a tracer of vehicle exhaust in Shanghai [28,29]. Research about VOCs in China mainly concentrated on economically developed areas; a few studies were implemented in Yibin city, but there was still a lack of results on the contribution of local VOCs to the formation of second pollutants. As a very fast-growing city in Sichuan province, Yibin is located in the south of Sichuan Basin, which suffers unfavorable topographic and meteorological conditions, and it is also an important sink for pollutants in Sichuan Basin [30]. With rapid economic growth, emissions from human activities are sticky problems to handle, and Yibin has become one of the most heavily polluted cities in these years. Research about VOCs in China mainly concentrated on economically developed areas and megacities, but few studies were implemented in these mid-sized cities. Therefore, our study on VOC characteristics and sources in Yibin has a certain reference value for other cities with the same pollution characteristics.
The data for this research were received from national monitoring stations for hourly VOC data, which was mainly used to figure out the basic properties and source apportionment of seasonal VOCs in Yibin. Firstly, we classified the 112 VOCs into five categories (e.g., alkanes, alkenes, aromatics, halohydrocarbons, and OVOCs), and cleared out the major species that contributed to the measurements of VOCs. Secondly, positive matrix factorization (PMF) was conducted to identify the seasonal source apportionment of VOCs, and tried to figure out the main emissions of ambient VOC mixing ratios in Yibin. Finally, domestic maximum incremental reactivity (MIR), OH reactive rates (K OH ), and fractional aerosol coefficient (FAC) values were used to calculate the ozone formation potential (OFP), OH radical lose rates (L OH ), and secondary organic aerosol formation potential (SOAP) of VOCs, and then aimed at the PMF results to distribute the source percentages into OFPs and SOAPs. Based on the analysis of these results, it is significant for policymakers to implement instructive plans to effectively reduce emissions in Yibin.

On-Line Sampling and Analysis
To better know the VOC characteristics in four seasons in Yibin, the VOC data we measured were from a long-term sampling site on the roof of a senior university. To facilitate the analysis, trace pollutant concentrations and meteorological data from the nearest state controlling monitoring stations were also obtained ( Figure 1). The three different sites we mentioned collected different monitoring data. The VOCs were enriched through a lowtemperature preconcentration unit (Models AC-GCMS1000, HEXIN MASS Spectrometry, Guangzhou, China) and analyzed by a gas chromatography-mass detector/flame ionization detector (GC-MS/FID, Models 7890A/59777B, Agilent, California, USA Because the reactions of VOCs with OH radicals are the starting points of photochemical oxidation for VOCs, the OH-responsive L OH becomes an important indicator of the VOC reactivates in a region, as shown in Equation (1): The maximum incremental reactivity (MIR) is commonly used to calculate the ozone formation potential (OFP) of each VOC species to indicate the maximum contribution of a single VOC species to ozone production, as shown in Equation (2): VOCs are essential contributors for forming secondary pollutants of SOA, and the FAC coefficient is universally used to calculate SOAPs, as shown in Equation (3): where SOAP means the SOA formed of VOC component i, [VOC] is the mixing ratio of

Ozone Formation Potential (OFP)
The maximum incremental reactivity (MIR) is commonly used to calculate the ozone formation potential (OFP) of each VOC species to indicate the maximum contribution of a single VOC species to ozone production, as shown in Equation (2): where OFP i is the ozone formation potential (µg/m 3 ) of VOC component i, [VOC] i is the mass mixing ratio (µg/m 3 ) of VOC species i in the measured atmospheric environment, and MIR i is the maximum incremental reactivity of VOC component i; the MIR i for 53 VOCs were obtained from the research team of Shandong University, which was developed on the domestic environment to better calculate OFP values [32].

Secondary Organic Aerosol Formation Potential (SOAP)
VOCs are essential contributors for forming secondary pollutants of SOA, and the FAC coefficient is universally used to calculate SOAPs, as shown in Equation (3): where SOAP i means the SOA formed of VOC component i, [VOC] i is the mixing ratio of VOC species i in an ambient atmosphere, F VOCr i is the fraction of reacted VOC species i, and FAC i represents the fractional aerosol coefficients from each VOC species, which were accessed by Grosjean [33].

Positive Matrix Factorization (PMF)
The PMF model is a conventional way to drill down VOC source apportionment and has been universally used in some research [34][35][36]. This study used the US EPA PMF 5.0 (Washington, DC, USA) model to analyze the main VOC sources in the spring, summer, fall, and winter, to show seasonal variation. Before running PMF, there are two input files need to be prepared, including a matrix of species concentrations and another matrix for concentration uncertainties. The uncertainty is determined by the relation between the concentration and MDL of VOC species; if the concentration is higher, the uncertainty values could be calculated by Equation (4), and otherwise by Equation (5): where MDL represents the method detection limit, and the error fraction represents the relative measurement error (as 10% in this study). After inputting the VOC data, the model can calculate the S/N (signal-to-noise ratio) values for each species, and there is a correction in the calculation of S/N values in PMF 5.0. In the corrected calculation, only the concentration values that exceed the uncertainty are included in the calculation, affecting the S (signal value) part of the S/N calculation. S/N < 1 is classified as "weak", and S/N > 1 is classified as "strong". In addition, the classification of species can also be set according to the data quality of a species in the actual observation, such as the time series of species' concentration, the scatter plot of concentration and uncertainty, and the correlation between species.
In the data processing, the VOC data in April, July, October and January were applied to represent the overall level in spring, summer, fall. and winter, respectively.

Basic Data Analysis
The factors that influence the urban air pollution situation were not only the emission sources and the pollution characteristics of the pollutants, but also the meteorological parameters. As provided in Figure S1, the variation in the daily average values of the main meteorological parameters during the observation period was given, and the average temperature in the four seasons was the lowest in winter 2022, 8.8 • C, varying between 7.7-10.9 • C, and the highest in summer 2021, 27.2 • C, varying between 23.7-30.8 • C. It could not be seen that the temperature and humidity showed a more obvious negative correlation with the variation of wind speed in Yibin's urban area in each season. A total of 112 VOC species monitored by the online equipment (Table S1) were divided into five categories: alkanes, alkenes, aromatics, halohydrocarbons, and OVOCs. Figure 2 shows the changes in mixing ratios and the percentage of components at the VOC component monitoring sites in April (spring), July (summer), October (fall), and January (winter). Figure 3 shows that alkanes account for more than 50%, and the largest share is in spring and winter, with average mixing ratios of 11.5 ppbv and 14.0 ppbv, respectively; OVOCs are the largest mixing ratio component in summer, with an average mixing ratio of 8.2 ppbv, and alkanes are second only to OVOCs, with an average mixing ratio of 7.2 ppbv. To further explore the dominant species of specific VOCs, as shown in Figure 4, the species in different seasons were basically the same, accounting for about 70% of the total VOCs; the dominant species of VOCs in Yibin urban area were mainly C 2 -C 5 alkanes. Ethane was the most dominant species in winter, spring, and fall, with average mixing ratios up to 7.1 ppbv, 4.4 ppbv, and 4.6 ppbv, while acetone was the most dominant species in summer, with mixing ratios up to 3.4 ppbv. The greatest variation in mixing ratio among the seasons was observed for acetaldehyde and ethylene, with acetaldehyde in summer (1.8 ppbv) being 3.2 times higher than in winter, 2.1 times higher than in fall, and 1.8 times higher than in spring, and ethylene in winter (3.2 ppbv) being 3.0 times higher than in summer, 2.7 times higher than in spring, and 2.7 times higher than in fall. Among the main dominant species, acetaldehyde and acetone had higher mixing ratios in summer than in the rest of the seasons, and the rest of the dominant species were all higher in winter than in the rest of the seasons. acetaldehyde in summer (1.8 ppbv) being 3.2 times higher than in winter, 2.1 times higher than in fall, and 1.8 times higher than in spring, and ethylene in winter (3.2 ppbv) being 3.0 times higher than in summer, 2.7 times higher than in spring, and 2.7 times higher than in fall. Among the main dominant species, acetaldehyde and acetone had higher mixing ratios in summer than in the rest of the seasons, and the rest of the dominant species were all higher in winter than in the rest of the seasons.   3.0 times higher than in summer, 2.7 times higher than in spring, and 2.7 times higher than in fall. Among the main dominant species, acetaldehyde and acetone had higher mixing ratios in summer than in the rest of the seasons, and the rest of the dominant species were all higher in winter than in the rest of the seasons.

Diurnal Variation Characteristics
The daily variation characteristics of atmospheric pollutants were the result of a combination of meteorological, primary emission, and atmospheric chemical processes. The diurnal variability of typical VOCs near the observation site was illustrated in Figure 5. The diurnal variation of VOC species could be affected by abundant factors, and the features of diurnal changes could also display the transportation, sources, and chemical reaction of ambient VOCs [37]. Overall, evening peak values of TVOCs, except for halohydrocarbons, were higher than their morning peak values. This was maybe caused by the lower boundary layer height at night than daytime, which was adverse for the vertical and mixed spreading out of VOC pollutants [38][39][40].
Atmosphere 2022, 13, x FOR PEER REVIEW

Diurnal Variation Characteristics
The daily variation characteristics of atmospheric pollutants were the result of bination of meteorological, primary emission, and atmospheric chemical processe diurnal variability of typical VOCs near the observation site was illustrated in Fig  The diurnal variation of VOC species could be affected by abundant factors, and t tures of diurnal changes could also display the transportation, sources, and chem action of ambient VOCs [37]. Overall, evening peak values of TVOCs, except for h drocarbons, were higher than their morning peak values. This was maybe caused lower boundary layer height at night than daytime, which was adverse for the v and mixed spreading out of VOC pollutants [38][39][40].
It could be seen that the seasonal daily variation of alkanes species was basical sistent, with the peak in spring occurring 2-3 h later than the other seasons, and on obvious peak was caused by the high emission of 3-methylpentane at 14:00, wh other seasons showed two peaks, with more prominent emissions at night (21:00 and early morning (8:00-12:00). The average hourly mixing ratio in winter was s cantly higher than the other seasons.
The daily trend of alkenes species showed a good consistency with two peaks, were more prominent in the morning (8:00) and evening (22:00-1:00). The lowest was reached in the afternoon (16:00), and the average hourly mixing ratios in winte much higher than those in other seasons.
The daily variation trend of aromatics species season showed a good consis and generally appears with multiple peaks, and the daily variation trend was mor sistent with CO and NO2: the first peak occurs in the early morning (8:00-11:00), was consistent with the morning rush hour, and was a typical traffic source emissio acteristic, and the peak point of emission occurs in the evening (21:00-22:00). The h point of variation appeared at 1:00 a.m. There may be nighttime industrial solven cessing at this site, which may also be caused by the reduced boundary layer mixin at night.
The daily variation in OVOC species was characterized by a single peak, wh curs after midday, similar to the trend in daily variation in the ozone. The peak of O It could be seen that the seasonal daily variation of alkanes species was basically consistent, with the peak in spring occurring 2-3 h later than the other seasons, and only one obvious peak was caused by the high emission of 3-methylpentane at 14:00, while the other seasons showed two peaks, with more prominent emissions at night (21:00-1:00) and early morning (8:00-12:00). The average hourly mixing ratio in winter was significantly higher than the other seasons.
The daily trend of alkenes species showed a good consistency with two peaks, which were more prominent in the morning (8:00) and evening (22:00-1:00). The lowest value was reached in the afternoon (16:00), and the average hourly mixing ratios in winter were much higher than those in other seasons.
The daily variation trend of aromatics species season showed a good consistency, and generally appears with multiple peaks, and the daily variation trend was more consistent with CO and NO 2 : the first peak occurs in the early morning (8:00-11:00), which was consistent with the morning rush hour, and was a typical traffic source emission characteristic, and the peak point of emission occurs in the evening (21:00-22:00). The highest point of variation appeared at 1:00 a.m. There may be nighttime industrial solvent processing at this site, which may also be caused by the reduced boundary layer mixing ratio at night.
The daily variation in OVOC species was characterized by a single peak, which occurs after midday, similar to the trend in daily variation in the ozone. The peak of OVOCs occurs at the same time as the trough of CO, and the increasing trend of OVOCs in the morning was associated with not only the secondary oxidation reaction [41,42] but also primary anthropogenic emissions. Moreover, the mixing ratio of OVOCs decreased continuously from 1:00 a.m. to 6:00 a.m., and showed a larger decrease at 7:00. The mixing ratios of OVOCs continued to decrease from 1:00 a.m. to 6:00 a.m., and then increased significantly from 7:00 a.m. to 16:00 a.m. to 18:00 a.m. After reaching their peak point, they maintained a stable change. The mixing ratio levels of OVOCs remained high at night, which may be due to the accumulation of NMHCs or the weakening of the photochemical reaction of OVOCs themselves. In addition, the decrease in the height of the mixed boundary layer during this time may also cause the pollutant mixing ratios to increase. morning was associated with not only the secondary oxidation reaction [41,42] but als primary anthropogenic emissions. Moreover, the mixing ratio of OVOCs decreased con tinuously from 1:00 a.m. to 6:00 a.m., and showed a larger decrease at 7:00. The mixin ratios of OVOCs continued to decrease from 1:00 a.m. to 6:00 a.m., and then increase significantly from 7:00 a.m. to 16:00 a.m. to 18:00 a.m. After reaching their peak point, the maintained a stable change. The mixing ratio levels of OVOCs remained high at nigh which may be due to the accumulation of NMHCs or the weakening of the photochemica reaction of OVOCs themselves. In addition, the decrease in the height of the mixed bound ary layer during this time may also cause the pollutant mixing ratios to increase.

Source Apportionment of VOCs in Yibin
To better know the potential reason for regional pollution and to implement contro strategies, it was appropriate to judge regional VOCs source contributions [43]. For th data analysis of VOCs in four seasons, 61 characteristic VOCs species were selected an input into the PMF model, and five types of source factors were resolved by error analysi and ordered the same in four seasons; the specific mixing ratio and percentage of PM

Source Apportionment of VOCs in Yibin
To better know the potential reason for regional pollution and to implement control strategies, it was appropriate to judge regional VOCs source contributions [43]. For the data analysis of VOCs in four seasons, 61 characteristic VOCs species were selected and input into the PMF model, and five types of source factors were resolved by error analysis and ordered the same in four seasons; the specific mixing ratio and percentage of PMF results in different seasons are provided in Table S2, and the concise graphs are shown in Figures 6-9.     Source 1 (Figures 6a, 7a, 8a and 9a) was assigned to solvent utilization, which contained high loadings of aromatics (ethylbenzene, toluene, o-xylene, m/p-xylene), ethyl acetate, and a certain level of long-chain alkanes. Ethyl acetate was a typical component of VOCs emitted from furniture spraying/oil-based paint [44], and toluene was usually used as an organic solvent species [45], so factor 1 was judged to be solvent utilization sources.     Source 2 (Figures 6b, 7b, 8b and 9b) was assigned to diesel vehicles, which had a high content of high-C number alkanes (octane and nonane) and aromatics (benzene and toluene). These compounds are typical emissions of diesel vehicles [46], so factor 2 was judged as diesel vehicle sources.
Source 3 (Figures 6c, 7c, 8c and 9c) was characterized by high contents of low-carbon alkanes (ethane, propane, isobutane, n-butane, and pentane), (z)-2-butene, and tert-butyl methyl ether, indicating that it was related to gasoline vehicle emissions. Ethylene and propylene were produced by internal combustion engines, and tert-butyl methyl ether was used as an addictive to improve the anti-knock performance of gasoline [47]. The results suggest that factor 3 was gasoline vehicle sources.
As shown in Figure 11, the diurnal variation in solvent utilization has a decrease in VOC concentrations in the early morning, which was likely due to enhanced photochemical loss and decreased emissions, and then the concentration of solvent emissions increased from 15:00 to 17:00. For diesel vehicle emissions, the source contribution has a sudden increase from 8:00 until 18:00, which was consistent with the human work schedule, with high loadings during the daytime and low loadings at nighttime. Gasoline vehicles showed two distinct peaks during the morning and evening, which were in line with rush hour traffic. It can be seen that the first peak appeared at about 9:00 and the second appeared at around 21:00 in four seasons due to a reduced mixing height and strengthened traffic emissions. Industrial manufacturing indicated that other seasons besides summer were characterized by high VOC concentrations during the afternoon due to high emissions and low concentrations during nighttime. Regional background and secondary formation emissions exhibited a maintenance of the VOC concentration level until midnight.

L OH of VOC Species
The total OH loss rates (L OH ) of the measured VOC species in this work were 2.9 s −1 , 4.4 s −1 , 2.0 s −1 , and 2.5 s −1 in spring, summer, fall, and winter, respectively (Table S3). Alkenes were the main reactive VOC group (Table S2). The alkenes accounted for 4.7%, 3.6%, 5.6%, 7.4% of TVOCs in spring, summer, fall, and winter, respectively, but they had the highest contribution to L OH , and their contributions to L OH were 27.7%, 22.6%, 36.8%, 47.3% in the four seasons, respectively. The higher mixing ratio of alkanes had a relatively small contribution to L OH , while halohydrocarbons had the lowest contribution to L OH . As shown in Figure 11, the diurnal variation in solvent utilization has a decrease in VOC concentrations in the early morning, which was likely due to enhanced photochemical loss and decreased emissions, and then the concentration of solvent emissions increased from 15:00 to 17:00. For diesel vehicle emissions, the source contribution has a sudden increase from 8:00 until 18:00, which was consistent with the human work schedule, with high loadings during the daytime and low loadings at nighttime. Gasoline vehicles showed two distinct peaks during the morning and evening, which were in line with rush hour traffic. It can be seen that the first peak appeared at about 9:00 and the second appeared at around 21:00 in four seasons due to a reduced mixing height and strengthened traffic emissions. Industrial manufacturing indicated that other seasons besides summer were characterized by high VOC concentrations during the afternoon due to high emissions and low concentrations during nighttime. Regional background and secondary formation emissions exhibited a maintenance of the VOC concentration level until midnight.  As shown in Figure 11, the diurnal variation in solvent utilization has a decrease in VOC concentrations in the early morning, which was likely due to enhanced photochemical loss and decreased emissions, and then the concentration of solvent emissions increased from 15:00 to 17:00. For diesel vehicle emissions, the source contribution has a sudden increase from 8:00 until 18:00, which was consistent with the human work schedule, with high loadings during the daytime and low loadings at nighttime. Gasoline vehicles showed two distinct peaks during the morning and evening, which were in line with rush hour traffic. It can be seen that the first peak appeared at about 9:00 and the second appeared at around 21:00 in four seasons due to a reduced mixing height and strengthened traffic emissions. Industrial manufacturing indicated that other seasons besides summer were characterized by high VOC concentrations during the afternoon due to high emissions and low concentrations during nighttime. Regional background and secondary formation emissions exhibited a maintenance of the VOC concentration level until midnight. Among the top ten species contributing to L OH (Figure 12a-d), ethylene contributed the most to L OH in spring, fall, and winter, because of the high-rate constant, while in summer, acetaldehyde ranked first.

OFP of Ambient VOCs
To estimate the contribution to the formation of O 3 at the ground level, the OFP method was applied in this work. The OFP values calculated included 53 VOC species (Table S4). As shown in Figure 13, alkenes and OVOCs were the major contributors to OFP in all seasons. Although, alkenes and OVOCs had a lower proportion of the TVOC mixing ratio, they were considered to play significant roles in O 3 formation [51]. 5.6%, 7.4% of TVOCs in spring, summer, fall, and winter, respectively, but they had the highest contribution to L OH , and their contributions to L OH were 27.7%, 22.6%, 36.8%, 47.3% in the four seasons, respectively. The higher mixing ratio of alkanes had a relatively small contribution to L OH , while halohydrocarbons had the lowest contribution to L OH .
Among the top ten species contributing to L OH (Figure 12a-d), ethylene contributed the most to L OH in spring, fall, and winter, because of the high-rate constant, while in summer, acetaldehyde ranked first.

OFP of Ambient VOCs
To estimate the contribution to the formation of O3 at the ground level, the OFP method was applied in this work. The OFP values calculated included 53 VOC species (Table S4). As shown in Figure 13, alkenes and OVOCs were the major contributors to OFP in all seasons. Although, alkenes and OVOCs had a lower proportion of the TVOC mixing ratio, they were considered to play significant roles in O3 formation [51].
The top ten VOC species contributing to total OFPs were given in Figure 14a-d. These species contributed the majority of the total OFPs, with contributions of 66.7%, 68.4%, 63.0%, and 69.6% in spring, summer, fall, and winter, respectively. Controlling these target VOC emissions would likely have a positive impact on O3 abatement [19]. Among the top ten OFP contributors, ethylene and acetaldehyde showed higher photochemical reaction reactivity and contributed most of the OFP. Isoprene, as a marker of biogenic VOCs, showed certain high OFPs in summer, which indicated that biogenic emissions might have significant roles in the formation of ground-level O3 in Yibin.  The top ten VOC species contributing to total OFPs were given in Figure 14a-d. These species contributed the majority of the total OFPs, with contributions of 66.7%, 68.4%, 63.0%, and 69.6% in spring, summer, fall, and winter, respectively. Controlling these target VOC emissions would likely have a positive impact on O 3 abatement [19]. Among the top ten OFP contributors, ethylene and acetaldehyde showed higher photochemical reaction reactivity and contributed most of the OFP. Isoprene, as a marker of biogenic VOCs, showed certain high OFPs in summer, which indicated that biogenic emissions might have significant roles in the formation of ground-level O 3 in Yibin.

SOAP of VOCs
The calculated SOAP values were 0.25 μg/m 3 , 0.34 μg/m 3 , 0.39 μg/m 3 , and 0.16 in spring, summer, fall, and winter, respectively (Table S5). The most important co tors to SOA were aromatics. The top ten VOC species contributing to the total SO listed in Figure 15a-d. The VOC species with the largest contribution to SOA in all s

SOAP of VOCs
The calculated SOAP values were 0.25 µg/m 3 , 0.34 µg/m 3 , 0.39 µg/m 3 , and 0.16 µg/m 3 in spring, summer, fall, and winter, respectively (Table S5). The most important contributors to SOA were aromatics. The top ten VOC species contributing to the total SOAP are listed in Figure 15a-d. The VOC species with the largest contribution to SOA in all seasons were toluene, m/p-xylene, and o-xylene. Generally, the formation of SOA was considered to be characterized mainly by aromatics [52,53]. Therefore, proper controlling of these compounds would have positive impacts on secondary pollution control. were toluene, m/p-xylene, and o-xylene. Generally, the formation of SOA was considered to be characterized mainly by aromatics [52,53]. Therefore, proper controlling of these compounds would have positive impacts on secondary pollution control.

Contributions of VOC Sources to the Secondary Pollutant Formation
In Sections 3.4.2 and 3.4.3, we have discussed the O3 formation potential of applying the MIR method to assess the reactivates of the VOC species, and discussed the SOA formation potential of applying the FAC method to assess the reactivates of the VOC species. Here, we tried to evaluate the O3 and SOA formation potential for each source depending on the concentration profile of each VOC species in the corresponding source derived from PMF model [54]. Therefore, we used the same method to calculate the contributions

Contributions of VOC Sources to the Secondary Pollutant Formation
In Sections 3.4.2 and 3.4.3, we have discussed the O 3 formation potential of applying the MIR method to assess the reactivates of the VOC species, and discussed the SOA formation potential of applying the FAC method to assess the reactivates of the VOC species. Here, we tried to evaluate the O 3 and SOA formation potential for each source depending on the concentration profile of each VOC species in the corresponding source derived from PMF model [54]. Therefore, we used the same method to calculate the contributions of VOC sources to O 3 and SOA formation. Figure 16a,c,e,g, presented the contributions of different VOC sources extracted from PMF to the OFP values in different seasons, respectively. In spring, solvent utilization had the largest OFPs (36.8 µg/m 3 ), accounting for 30.4% of the total OFP values. This was due to the high loadings of relative aromatics in this source profile, followed by gasoline vehicles (32.2 µg/m 3 , 26.6%), industrial manufacturing (30.6 µg/m 3 , 25.2%), regional background and secondary formation (14.0 µg/m 3 , 11.5%), and diesel vehicles (7.7 µg/m 3 , 6.4%). In summer, the OFP value of industrial manufacturing became the highest (39.4 μg/m 3 ), and the proportion increased to twice that value in summer (27.7%). The order of contribution of the other sources to OFP was greatly changed, followed by solvent utilization (28.9 μg/m 3 , 20.3%), diesel vehicles (27.8 μg/m 3 , 19.5%), gasoline vehicles (26.5 μg/m 3 , 18.6%), and regional background and secondary formation (29.6 μg/m 3 , 13.8%). In all, the contributions of OFPs from the regional background was stable.
In the winter, gasoline vehicles had the largest proportion of OFPs (48.2 μg/m 3 , 39.5%), followed by solvent utilization (21.3 μg/m 3 , 17.5%), diesel vehicles (20.3 μg/m 3 , 16.7%), industrial manufacturing (16.1 μg/m 3 , 13.2%), and regional background and secondary formation (16.0 μg/m 3 , 13.1%). All in all, gasoline vehicles contributed the most of OFPs; therefore, proper controlling of gasoline vehicle emissions matters to the management of VOCs to reduce the formation of O3 and photochemical pollution in Yibin city. Figure 16b,d,f,h showed the top ten OFP contributors of VOCs from different sources. We found that m/p-xylene, ethylene from the emissions of solvent utilization, 2-methyl- In summer, the OFP value of industrial manufacturing became the highest (39.4 µg/m 3 ), and the proportion increased to twice that value in summer (27.7%). The order of contribution of the other sources to OFP was greatly changed, followed by solvent utilization (28.9 µg/m 3 , 20.3%), diesel vehicles (27.8 µg/m 3 , 19.5%), gasoline vehicles (26.5 µg/m 3 , 18.6%), and regional background and secondary formation (29.6 µg/m 3 , 13.8%). In all, the contributions of OFPs from the regional background was stable.
In the winter, gasoline vehicles had the largest proportion of OFPs (48.2 µg/m 3 , 39.5%), followed by solvent utilization (21.3 µg/m 3 , 17.5%), diesel vehicles (20.3 µg/m 3 , 16.7%), industrial manufacturing (16.1 µg/m 3 , 13.2%), and regional background and secondary formation (16.0 µg/m 3 , 13.1%). All in all, gasoline vehicles contributed the most of OFPs; therefore, proper controlling of gasoline vehicle emissions matters to the management of VOCs to reduce the formation of O 3 and photochemical pollution in Yibin city. Figure 16b,d,f,h showed the top ten OFP contributors of VOCs from different sources. We found that m/p-xylene, ethylene from the emissions of solvent utilization, 2-methylbutane and 1,2,4-trimethylbenzene from industrial manufacturing, acetaldehyde, and ethylene from diesel vehicles were the main species of VOC emissions contributing to the formation of the photochemical O 3 . Therefore, the emissions of specific VOC species should not be ignored, though there was a small amount of VOC species that could be monitored to effectively alleviate photochemical pollution in Yibin. Solvent utilization contributed most in the spring, fall, and winter, which indicated that during these periods, there was a need to focus more on the mixing ratio of aromatics, as the source of aromatics was mainly from solvent utilization. Figure 17a,c,e,g present the contributions of different VOC sources extracted from PMF to the SOAP values in different seasons, respectively.  Generally, the results showed that the proportion and SOAP value of solvent utilization sources followed the sequence of spring (0.3 μg/m 3 , 50.6%) > fall (0.2 μg/m 3 , 45.8%) > winter (0.2 μg/m 3 , 38.3%) > summer (0.1 μg/m 3 , 31.3%). During spring and fall, solvent utilization made the dominant contribution to SOAPs, which may be affected by the temperature of these two seasons. When it came to diesel vehicle sources, the proportion sequence changed into fall (16.2%) > summer (8.9%) > winter (7.9%) > spring (7.0%), while the SOAP value of diesel vehicles was similar during fall (0.07 μg/m 3 ), summer (0.05 μg/m 3 ), winter (0.05 μg/m 3 ), all better than spring (0.04 μg/m 3 ). Gasoline vehicles had the order of spring (30.5%) > winter (23.3%) > summer (22.5%) > fall (15.5%). The proportion sequence from industrial manufacturing was summer (39.6%) > spring (16.0%) > winter (15.2%) > fall (6.3%), while the SOAP value in summer (0.30 μg/m 3 ) was the largest. The proportion order of regional background and secondary formation was fall (9.2%) > win- Generally, the results showed that the proportion and SOAP value of solvent utilization sources followed the sequence of spring (0.3 µg/m 3 , 50.6%) > fall (0.2 µg/m 3 , 45.8%) > winter (0.2 µg/m 3 , 38.3%) > summer (0.1 µg/m 3 , 31.3%). During spring and fall, solvent utilization made the dominant contribution to SOAPs, which may be affected by the temperature of these two seasons. When it came to diesel vehicle sources, the proportion sequence changed into fall (16.2%) > summer (8.9%) > winter (7.9%) > spring (7.0%), while the SOAP value of diesel vehicles was similar during fall (0.07 µg/m 3 ), summer (0.05 µg/m 3 ), winter (0.05 µg/m 3 ), all better than spring (0.04 µg/m 3 ). Gasoline vehicles had the order of spring (30.5%) > winter (23.3%) > summer (22.5%) > fall (15.5%). The proportion sequence from industrial manufacturing was summer (39.6%) > spring (16.0%) > winter (15.2%) > fall (6.3%), while the SOAP value in summer (0.30 µg/m 3 ) was the largest. The proportion order of regional background and secondary formation was fall (9.2%) > winter (8.2%) > summer (4.8%) > spring (3.1%), while the SOAP value in winter (0.04 µg/m 3 ) and summer (0.04 µg/m 3 ) were larger than other two seasons. More focus should be put on industrial manufacturing emissions in summer for their high contribution to SOAPs. Figure 17b,d,f,h showed the top ten SOAP contributors of VOCs from different sources. We found that m/p-xylene from the emissions of solvent utilization and toluene from gasoline vehicle were the main species of VOC emissions contributing to the formation of SOA. Therefore, in order to reduce SOA formation in Yibin, emissions of VOCs in gasoline vehicles and solvent utilization should be reduced as far as possible. When analyzing the local secondary pollution situation in Yibin city, it was not only necessary to consider the mixing ratio of VOCs, but also to focus on identifying the sources that have the greatest impact on local emissions, and then to analyze the specific VOC species from the sources to achieve the precise and effective control of local secondary pollution status.
Additionally, five sources were received from the PMF model. The results showed that vehicle sources including gasoline and diesel vehicles together contributed the most VOCs in all seasons, and the percentages of each season fluctuated between 30.5% and 40.1%. Solvent utilization was also important in emissions, which had the ratio of 16.5-27.6% in four seasons, the proportion of industrial manufacturing changed between 18.9-23.7%, and regional background and secondary formation accounted for 18.2-28.3% in different seasons.
Through the calculation of OFPs and SOAPs, we could initially find that m/p-xylene, toluene, and ethylene contribute a larger proportion of all the species mentioned above. As for the source contributions to OFPs and SOAPs, we found that contributions to secondary pollutants by different sources varied across seasons. In spring, solvent utilization (OFP 30.4%; SOAP 50.6%) was the dominant source, followed by gasoline vehicles (OFP 26.6%; SOAP 23.3%) and industrial manufacturing (OFP 25.2%; SOAP 16.0%); in summer, the major source was gasoline vehicles (OFP 26.6%; SOAP 15.5%) and solvent utilization (OFP 20.3%; SOAP 31.3%); in fall, solvent utilization (OFP 34.7%; SOAP 45.8%) made the greatest contribution to secondary formation, followed by gasoline vehicles (OFP 28.3%; SOAP 22.5%); in winter, gasoline vehicles (OFP 39.5%; SOAP 30.5%) and solvent utilization (OFP 17.5%; SOAP 38.3%) were the dominant sources. In order to reduce the ambient VOCs to comply with the atmospheric standards, priority should be given to gasoline vehicle and solvent utilization emissions. Overall, all the studies are of benefit for the precise emission control of VOCs in the Yibin region, and are further useful for VOC emission control strategy in other cities.
Supplementary Materials: The following supporting information can be downloaded at: https:// www.mdpi.com/article/10.3390/atmos13091389/s1, Figure S1: Time series of Temperature and RH; Table S1: The measured VOCs species; Table S2: Source profiles calculated by PMF model; Table S3: The contributions of VOCs to LOH in spring, summer, fall, winter; Table S4: The contributions of VOCs to OFP in spring, summer, fall, winter; Table S5: The contributions of VOCs to SOAP in spring, summer, fall, winter.