Unraveling the Drivers of Continuous Summer Ozone Pollution Episodes in Bozhou, China: Toward Targeted Control Strategies

Abstract

Given the deteriorating situation of ambient ozone (O₃) pollution in some areas of China, understanding the mechanisms driving O₃ formation is essential for formulating effective control measures. This study examines O₃ formation mechanisms and RO_x (OH, HO_2, and RO₂) radical cycling driven by photochemical processes in Bozhou, located at the junction of Jiangsu–Anhui–Shandong–Henan (JASH), a region heavily affected by O₃ pollution, by applying a zero-dimensional box model (Framework for 0-Dimensional Atmospheric Modeling, F0AM) coupled with the Master Chemical Mechanism (MCM v3.3.1) and Positive Matrix Factorization (PMF 5.0) to characterize O₃ pollution, identify volatile organic compound (VOC) sources, and quantify radical budgets during pollution episodes. The results show that O₃ episodes in Bozhou mainly occurred in June under conditions of high temperature and low wind speed. Oxygenated volatile organic compounds (OVOCs), alkanes, and halocarbons were the dominant VOCs groups. The CH₃O₂ + NO reaction accounted for 24.3% of O₃ production, while photolysis contributed 68.7% of its removal. Elevated VOCs concentrations in Bozhou were largely maintained by anthropogenic sources such as vehicle exhaust, solvent utilization, and gasoline evaporation, which collectively enhanced O₃ production. The findings indicate that O₃ formation in the region is primarily regulated by NO_x availability. Therefore, emission reductions targeting NO_x, along with selective control of OVOCs and alkenes, would be the most effective strategies for lowering O₃ levels. Model simulations further highlight Bozhou’s strong atmospheric oxidation capacity, with OVOC photolysis identified as the dominant contributor to RO_x generation, accounting for 33% of the total. Diurnal patterns were evident: NO_x-related reactions dominated radical sinks in the morning, while HO₂ + RO₂ reactions accounted for 28.5% in the afternoon. By clarifying the mechanisms of O₃ formation in Bozhou, this study provides a scientific basis for designing ozone control strategies across the JASH junction region. In addition, ethanol was not directly measured in this study; given its potential to generate acetaldehyde and affect local O₃ formation, its possible contribution introduces additional uncertainty that warrants further investigation.

1. Introduction

Since the implementation of the “Air Pollution Prevention and Control Action Plan” and the “Three-Year Action Plan to Win the Blue Sky Defense War” [1,2], significant progress has been achieved in mitigating PM_2.5 pollution across China. However, the rising trend in O₃ concentrations has not been effectively mitigated [3,4]. From 2015 to 2019, China experienced a pronounced increase in O₃ pollution. The proportion of days dominated by O₃ exceedance increased from 16.9% to 41.8%, and 103 cities exceeded the national O₃ standard [5,6]. The observed pattern aligns with broader global trends, where background O₃ levels have shown a steady upward trajectory over recent decades, indicative of a strengthened atmospheric oxidizing environment. Long-term monitoring supports this rise; for instance, Sicard [7] documented average annual O₃ growth rates of about 0.15 ppbv in background regions and nearly double that, 0.31 ppbv, in urban environments. At the hemispheric scale, background O₃ continues to increase, providing important context for regional pollution. In the mid-latitudes of the Northern Hemisphere, surface O₃ exhibited an average annual growth rate of about 1% [8], while five of the seven long-term monitoring sites in the Southern Hemisphere reported decadal mean increases of 0.5–2 ppbv [9]. This large-scale enhancement of background O₃ has also been reflected in China, where O₃ concentrations have shown a persistent upward trend with pronounced spatial heterogeneity. At the Waliguan global background station in western China, O₃ increased at an average rate of 0.2 ± 0.3 ppbv/year [10]. Long-term records further indicate significant increases across both diurnal and seasonal cycles, with growth rates of 0.24 ppbv/year during daytime, 0.28 ppbv/year at night, 0.24, 0.22, 0.29, and 0.13 ppbv/year in spring, summer, autumn, and winter, respectively [10,11,12,13]. Faster increases have been observed in regions with intensive anthropogenic activity and dense urbanization. For example, the Taishan site on the North China Plain recorded a summer O₃ increase of 2.2 ± 1.2 ppbv/year [10], while the Hong Kong site reported a rate of 0.54 ± 0.49 ppbv/year [14]. Overall, these findings demonstrate a clear and sustained rise in O₃ levels in China over recent decades, driven by both regional photochemistry and enhanced hemispheric background O₃.

The junction of Jiangsu–Anhui–Shandong–Henan (JASH) provinces, situated between the Beijing–Tianjin–Hebei region and the Yangtze River Delta, also experiences severe O₃ pollution. However, research on O₃ formation mechanisms in China has primarily concentrated on major urban clusters, including the Pearl River Delta [15,16], the Yangtze River Delta [17], the North China Plain [18], and the Sichuan–Chongqing region [19,20,21]. In many urban settings, O₃ production is primarily constrained by the availability of volatile organic compounds (VOCs), while suburban and rural regions tend to be governed by NO_x limitations or exist within an intermediate sensitivity regime. Modeling results from Nanjing highlight this contrast, showing that on days when O₃ levels surpassed the standard, the atmosphere exhibited a substantially higher oxidative capacity, reflected in OH and HO₂ concentrations that were 1.6- and 1.7-fold greater than those on non-exceedance days [22]. Similarly, Wang et al. [23], using the Photochemical Box Model–Master Chemical Mechanism (PBM-MCM), reported that the South China Sea region operates under a transitional regime between VOC and NO_x limitation on non-exceedance days, but shifts to VOC-limited conditions on O₃ exceedance days. During exceedance days, enhanced photochemical cycling led to an average daytime net O₃ production rate 3.2 times higher than on non-exceedance days. These results highlight that radical concentrations are influenced not only by the composition and abundance of VOCs but also by solar radiation intensity, both of which jointly regulate ambient O₃ levels. Lyu et al. [18] further investigated RO_x radical budgets and O₃ formation, identifying VOC-limited conditions in Wuhan during autumn, where HONO played a major role in enhancing atmospheric oxidative capacity. Although recent studies have addressed the characteristics of O₃ precursors [24], photochemical reaction mechanisms [25], and the influence of meteorology on O₃ pollution [26], the mechanisms of O₃ formation in the JASH junction remain insufficiently studied and poorly understood.

Bozhou, located at the JASH junction, possesses a strategically advantageous location and a distinctive industrial structure. It serves as a major national distribution center for traditional Chinese medicine and a renowned hub of the liquor industry. However, with the rapid progression of industrialization and urbanization, the city has been facing increasingly severe air pollution challenges. This study integrated meteorological observations, routine air pollutant measurements, and VOC monitoring at the Bozhou University site to investigate local O₃ pollution. In parallel, the F0AM model coupled with the MCM was employed to simulate O₃ formation and perform a comprehensive budget analysis. The findings aim to provide a scientific foundation for designing targeted strategies to mitigate O₃ pollution in Bozhou and the surrounding region.

2. Materials and Methods

2.1. Data Sources

The Air quality and meteorological data were obtained from the China National Environmental Monitoring Center (http://www.cnemc.cn/sssj/ (accessed on 25 July 2025)) and the Anhui Province Air Quality Forecasting and Early Warning Platform. The dataset includes hourly measurements of six conventional air pollutants (PM_2.5, PM₁₀, NO₂, SO₂, CO, and O₃), together with key meteorological parameters such as wind speed, wind direction, temperature, relative humidity, and atmospheric pressure. VOCs were measured at a comprehensive atmospheric supersite located at Bozhou University, which functions as a national intensive observation station and provides high-resolution in situ VOC observations. VOC measurements were conducted using an online gas chromatograph system (TH-300B, Wuhan Tianhong Instrument Co., Ltd., Wuhan, China) equipped with a GC–FID/MS configuration (7890B GC/5977B MSD, Agilent Technologies Inc., Santa Clara, CA, USA). Instrument operation and calibration followed national technical specifications (HJ/T 193-2005 and HJ 1010-2018; [27,28]), with full details provided in Supplementary Text S2. A map showing the study area and the location of the supersite is provided in the Supplement Figure S1. Pollution episodes were identified according to the China National Ambient Air Quality Standard. A pollution event was defined when either the 24 h average PM_2.5 concentration exceeded 75 µg/m³ or the maximum daily 8 h average (MDA8) O₃ exceeded 160 µg/m³ (≈75 ppbv), corresponding to the Grade II limits of GB 3095-2012 [29]. These observational datasets were subsequently used to initialize and constrain the zero-dimensional OBM, while detailed model configuration procedures are described in the Text S3.

2.2. Ozone Formation Potential

Ozone Formation Potential (OFP) is an indicator used to assess the capacity of VOCs to generate O₃ through photochemical reactions in the troposphere, helping to identify the species that contribute most significantly to O₃ formation. The OFP of individual VOC species was calculated using the following formula:

$$OF{P}_i=VOC{s}_i\times MI{R}_i$$

(1)

where VOCs_i is the ambient mass concentration of species i (μg/m³), and MIR_i is its maximum incremental reactivity (gO₃/gVOCs) [30]. The MIR coefficient represents the amount of ozone formed per unit mass of VOC under high-NO_x conditions and is a widely applied metric for evaluating the relative ozone-forming potential of VOCs. The MIR values used in this study were adopted from Carter’s reactivity scale, which was established based on detailed photochemical box-model simulations and has been extensively employed in ozone formation assessments [31]. It should be noted that IR values derived from the OBM may differ from MIR- or MOIR/EBIR-based ozone formation potentials due to differences in chemical mechanisms and NO_x regimes. A direct comparison with published reactivity scales would be valuable for assessing regime dependence and linking local photochemical responses to widely used metrics, and is suggested as a topic for future research.

2.3. Positive Matrix Factorization Model

The Positive Matrix Factorization (PMF) model, developed by the U.S. Environmental Protection Agency (EPA), has been extensively applied to identify sources of PM_2.5 and VOCs. It is important to note that the source profiles resolved by PMF are derived from statistical covariance structures within the input dataset. As a result, individual factors may represent mixed sources or reflect co-emitted pollutants originating from distinct but temporally correlated activities. Factor identification and naming were carried out by combining chemical marker analysis with previous knowledge of regional emission characteristics.

The PMF model is described by the following equation:

$$X_{ij}={\sum }_{k=1}^p{g}_{ik}{f}_{kj}+e_{ij}$$

(2)

where X_ij is the concentration of species j in sample i, in ppb; g_ik is the contribution of source k to sample i; f_ik is the source profile of species j in source k; e_if is the residual matrix of species j in sample i; and p is the number of factors. The PMF model primarily minimizes the objective function Q [32], which is defined as:

$$Q={\displaystyle \sum _{i=1}^n{\displaystyle \sum _{j=1}^m{\left(\frac{e_{ij}}{u_{ij}}\right)}^2}}$$

(3)

where n is the number of samples, m is the number of species, and u_ij represents the uncertainty of species in the samples.

When applying PMF to identify VOC sources, two input files are required: one containing the concentrations of the species (Conc.) and another containing their associated uncertainties (Unc.) [32,33]. The uncertainty of samples is calculated as follows:

$$Unc.=\left\{\begin{array}{cc}\sqrt{{\left(Error Fraction\times Conc.\right)}^2+{\left(0.5\times \mathrm{MDL}\right)}^2}& (Conc.>\mathrm{MDL})\\ 5\times \mathrm{MDL}/6\hfill & (Conc.\le \mathrm{MDL})\end{array}\right.$$

(4)

where MDL is the method detection limit. For concentrations below the MDL, a value equal to one-half of the MDL is substituted.

2.4. Observation-Based Model

To better understand the chemical mechanisms driving O₃ pollution in Bozhou and to assess how O₃ responds to reductions in its precursors, this study employed the observation-based model (OBM) F0AM to simulate atmospheric chemical processes. F0AM is a zero-dimensional box model constrained by observational data and driven by the MCM v3.3.1 [34,35,36]. The mechanism implemented in this study incorporates 5733 chemical species and 16,940 reactions, providing a comprehensive framework for simulating complex atmospheric chemistry. Details on model initialization, boundary layer assumptions, and the limitations of the F0AM simulations are presented in Supplementary Text S3. The input dataset for the F0AM model included the supersite’s geographic coordinates (latitude, longitude, and elevation), the observation period, hourly meteorological parameters (temperature, pressure, and relative humidity), concentrations of routine air pollutants (NO₂, NO, SO₂, CO, and O₃), and VOC speciation data. Since photolysis rates were not directly measured, they were estimated using the solar zenith angle parameterization provided within the MCM framework [34,36]. To evaluate the impacts of precursor emissions on ozone formation, multiple reduction scenarios were simulated. The model was further used to quantify ozone production rates, hydroxyl radical (OH) reactivity, and the primary pathways of production, recycling, and termination of RO_x radical species. OH reactivity was assessed based on its reaction kinetics with various atmospheric compounds, including VOCs, NO_x, CO, SO₂, nitric acid (HNO₃), and peroxynitric acid (HO₂NO₂).

The primary sources of OH, HO₂, and peroxy radicals (RO₂) include the photolytic decomposition of ozone, nitrous acid (HONO), acetaldehyde, and other OVOCs, along with reactions between VOCs and ozone or nitrate radicals. To evaluate the chemical budget of reactive RO_x radicals, following the approach of Wang et al. [37] and Xue et al. [38], the relevant reactions are categorized into three groups: major production, recycling, and removal pathways. Furthermore, the chemical budget of O₃ is analyzed using a modeling approach. The ozone production rate, P(O₃), is defined as the sum of the reaction rates of HO₂ with NO and RO₂ with NO (Equation (5)). The O₃ loss rate, L(O₃), is determined by adding the reaction rates of O₃ photolysis and its reactions with OH, HO₂, and NO₂ (Equation (6)). The net O₃ production rate is then obtained as the difference between P(O₃) and L(O₃) (Equation (7)). For clarity, only the key processes controlling O₃ formation and loss are briefly summarized here. The kinetic expressions in Equations (5) and (6) are derived from the MCM, and the dominant pathways involve HO₂/RO₂–NO interactions and NO₂ photolysis for O₃ production, as well as NO titration, photolysis, and radical-driven chemistry for O₃ loss. Detailed descriptions of these chemical calculations and the complete reaction framework are provided in the Text S4 and can also be found in the referenced literature [38,39]. It is important to note the limitations of the F0AM simulation. First, variations in planetary boundary layer dynamics are not explicitly represented, and thus vertical mixing effects, particularly during day–night transitions, may not be fully captured. Second, deposition is treated in a simplified manner, approximated as a uniform dilution process rather than being independently parameterized, which introduces uncertainty in simulating the diurnal evolution of pollutant concentrations and radical budgets.

$$P\left({\mathrm{O}}_3\right)=k_1\left[{\mathrm{HO}}_2\right][\mathrm{NO}]+{\displaystyle \sum \left(k_2\left[{\mathrm{RO}}_2\right][\mathrm{NO}]\right)}$$

(5)

$$\begin{array}{cc}\hfill L\left({\mathrm{O}}_3\right)& =k_3\left[\mathrm{O}{(}^1\mathrm{D})\right]\left[{\mathrm{H}}_2\mathrm{O}\right]+k_4\left[{\mathrm{O}}_3\right]\left[\mathrm{OH}\right]\hfill \\ & +k_5\left[{\mathrm{O}}_3\right]\left[{\mathrm{HO}}_2\right]+k_6\left[{\mathrm{NO}}_2\right]\left[{\mathrm{O}}_3\right]\hfill \end{array}$$

(6)

$$NetP\left({\mathrm{O}}_3\right)=P\left({\mathrm{O}}_3\right)-L\left({\mathrm{O}}_3\right)$$

(7)

The Empirical Kinetic Modeling Approach (EKMA) and Relative Incremental Reactivity (RIR) are valuable tools for examining the relationship between O₃ concentrations and their precursors, including VOCs and NO_x. These approaches provide a scientific basis for formulating effective O₃ pollution control strategies. Owing to the highly nonlinear interactions among O₃, VOCs, and NO_x, RIR is particularly effective in quantifying the sensitivity of O₃ formation to its precursors in a given region.

$$\mathrm{RIR}(X)={\displaystyle \frac{\left[P\left({\mathrm{O}}_3\right)\left(X\right)-P\left({\mathrm{O}}_3\right)(X-\Delta X)\right]/P\left({\mathrm{O}}_3\right)\left(X\right)}{\Delta c\left(X)/c\right(X)}}$$

(8)

In the equation, X denotes a precursor, c(X) indicates its observed concentration in the atmosphere, and Δc(X)/c(X) expresses the relative change resulting from variations in the volume fraction of precursor X. The subsequent term corresponds to the net O₃ production simulated by the F0AM model. In this study, RIR values were calculated by reducing the volume fraction of each precursor by 20%.

To evaluate the reliability of the model simulations, the Index of Agreement (IOA) was applied, following the formulation provided by Liu et al. [40].

$$IOA=1-{\displaystyle \frac{{\displaystyle \sum _{i=1}^n{\left(O_i-S_i\right)}^2}}{{\displaystyle \sum _{i=1}^n{\left(|O_i-\overline{O}|+|S_i-\overline{O}|\right)}^2}}}$$

(9)

where $S_i$ is the simulated value, $O_i$ is the observed value, $\overline{O}$ is the average observed value, and n is the number of samples. The IOA follows the standard formulation originally proposed by Willmott [41] and ranges from 0 to 1, with higher values representing stronger agreement between simulated and observed data. Previous atmospheric modeling studies suggest that IOA values in the range of 0.68–0.89 generally indicate satisfactory model performance [23,42]. In this study, the IOA was calculated as 0.87, which falls within the upper range of previously reported values, demonstrating that the F0AM model reliably reproduces the observed O₃ variations and is therefore suitable for subsequent radical analysis (Figure S2).

3. Results and Discussion

3.1. Overview of Ozone Pollution

From April to August 2023, a total of 32 days were classified as polluted in Bozhou, accounting for 20.9% of the monitoring period. On the majority of these days, O₃ was the primary pollutant, responsible for 81.3% of the recorded pollution events. The highest occurrence of O₃ pollution was recorded in June, with 16 exceedance days. A particularly severe and persistent episode unfolded from 8 to 16 June, during which the maximum daily 8 h average O₃ concentration (MDA8h O₃) peaked at 135.4 ppbv on 10 June. Owing to its intensity and duration, this nine-day episode was selected for detailed analysis of O₃ formation mechanisms.

During the O₃ pollution episode in Bozhou, MDA8h O₃ concentrations ranged from 94.3 to 135.4 ppbv, consistently exceeding the national secondary standard of 75 ppbv. O₃ formation was primarily driven by precursor availability and meteorological conditions, with daytime photochemical reactions serving as the dominant mechanism for O₃ accumulation. Meteorological conditions during this period were characterized by a maximum temperature of 38.6 °C, low average wind speeds of 1.4 ± 0.5 m/s, and moderate average relative humidity of 47.7 ± 17.3% (Table S1).

Figure 1 presents a at the Bozhou University monitoring site, the concentrations of NO₂, PM_2.5, and O₃ displayed similar temporal patterns and strong correlations, all statistically significant at the 0.01 level Figure S3a. The mean PM_2.5 concentration was 23.5 ± 11.5 μg/m³, while the average NO₂ concentration was 5.6 ± 2.8 ppbv. O₃ levels were substantially high, with the maximum 1 h concentration reaching 152.7 ppbv.

From a diurnal perspective (Figure 2), O₃ concentrations remain at relatively low levels from nighttime until approximately 09:00 local time (LT), after which they increase and reach a maximum around 17:00 LT. In contrast, VOCs, NO_x, and CO exhibit similar diurnal patterns, with higher concentrations during nighttime and lower concentrations during daytime. This behavior suggests that these precursors experience enhanced daytime removal, driven by a combination of photochemical processing and dilution associated with the daytime expansion of the planetary boundary layer, while accumulating at night under weaker mixing conditions. NO₂ displays a distinct temporal pattern, with concentrations peaking around 08:00 LT, decreasing between 09:00 and 16:00 LT, and rising again during the evening and nighttime. This diurnal characteristic is closely related to local traffic management policies, under which heavy-duty diesel trucks are restricted from entering the urban area during daytime and primarily operate at night, thereby highlighting their critical contribution to nighttime NO_x emissions. Bozhou’s location within the JASH junction, a major transport corridor connecting the Beijing–Tianjin–Hebei region with the Yangtze River Delta, further influences this trend. Road freight transport dominates the region, supported by a fleet of more than 2.4 million diesel trucks, which serve as a major source of NO_x emissions. The combined influence of emission patterns and boundary layer dynamics [43,44] explains the observed diurnal variations. NO₂ levels rose during morning and evening rush hours, followed by a pronounced decline at midday. NO exhibited sharp morning peaks that diminished rapidly. Across the study period, the mean daily concentrations were 5.4 ppbv for NO₂, 0.4 ppbv for NO, and 0.5 ppmv for CO.

Analysis of total VOCs (TVOCs) during the O₃ pollution episode revealed that alkanes were the predominant group, with the highest daily average concentration (6.8 ppbv) and relative contribution (33.3%), followed by oxygenated volatile organic compounds (OVOCs), halogenated hydrocarbons, and alkenes (Figure 3). The daily average concentration and proportion of alkanes peaked on 8 June and subsequently showed a fluctuating decline. Alkynes and aromatic hydrocarbons exhibited a steady upward trajectory over the course of the episode, peaking on 16 June with daily mean concentrations of 1.1 ppbv (5.1%) and 1.4 ppbv (6.7%), respectively. Further diagnostic analysis showed an ethylene/ethane ratio of 0.5 ± 0.4 in Bozhou, which was significantly lower (p < 0.01) than that reported for aged air masses in Hong Kong (0.7 ± 0.1) (Figure S3b). This finding suggests that the elevated O₃ levels in Bozhou were partly influenced by aged air masses, likely attributable to regional pollutant transport and/or enhanced in situ atmospheric oxidation [45].

Comparisons of TVOC concentrations during the pollution period indicate that Bozhou (19.8 ± 4.3 ppbv) has substantially lower levels than several major urban centers, including Beijing (44.2 ppbv), Chengdu (36.0 ppbv), Lanzhou (45.3 ppbv) [46], Nanjing (49.0 ppbv) [22], and Seoul (35.6 ppbv) [47]. The levels recorded in Bozhou exceeded those typically measured at background or remote sites, such as Taishan (8.8 ppbv) [48] and Waliguan (2.6 ppbv) [49]. They are, however, comparable to values reported in other medium-sized cities, including Luoyang (20.9 ppbv) [50] and Xi’an (19.0 ppbv) [51].

3.2. Ozone Formation Mechanisms

3.2.1. Ozone Formation Sensitivity

To investigate the relationship between O₃ and its precursors, an EKMA curve analysis was conducted (Figure 4a). During the pollution episode, most volume fraction points were located below the ridge line, with a smaller proportion situated near the VOC–NO_x transitional regime. This distribution indicates that local O₃ formation was primarily constrained by NO_x availability. The ridge line exhibited a slope of 0.4, indicating that the most effective and sustainable reduction in O₃ would result from precursor control strategies aligned with this trajectory, implementing VOCs and NO_x reductions at an approximate ratio of 0.4:1.

As shown in Figure 4b, NO_x exhibits the highest RIR value (0.89), indicating that reductions in NO_x emissions are most effective for mitigating local O₃ pollution. This finding is consistent with the results presented in Section 3.3. CO contributes negligibly to O₃ production, whereas VOCs play a more substantial role. Sensitivity analysis shows that anthropogenic VOCs (AVOCs) (excluding isoprene) have an RIR of 0.13, while biogenic VOCs (BVOCs), mainly isoprene, exert a stronger effect with an RIR of 0.23. The BVOC RIR in Bozhou is higher than values reported for Nanjing (0.12–0.13) [52] and is comparable to those observed in Shanghai [46].

As shown in Figure 4c, VOC components such as OVOCs, alkanes, and alkenes make substantial contributions to O₃ formation, consistent with the findings presented in Section 3.4. The RIR-based ranking of the top 10 VOC species, illustrated in Figure 4d, further highlights their relative importance. Among these, acetaldehyde, ethylene, and propylene emerge as the most influential precursors, underscoring their priority for targeted control measures in Bozhou. A broader comparison with results from major regions in China (

Table 1. Summary of O₃ formation sensitivity, key active VOCs species, and O₃ formation mechanisms in major regions of China.

Region	Site	Type	O3 Formation Regime	Dominant VOCs	References
Beijing-Tianjin-Hebei Province and surrounding areas	Beijin	Urban	VOC-limited	Alkenes	[53]
	Jinan	Urban	VOC-limited	Alkenes
	Baoding	Urban	VOC-limited	Aromatics	[54]
	Qingdao	Rural	Transition	Alkenes	[55]
	Yucheng	Rural	NOx-limited	BVOCs
	Wangdu	Suburban	Transition	Alkenes	[56]
Yangtze River Delta region	Nanjing	Industrial	VOC-limited	Alkenes, Aromatics	[57]
	Shanghai	Urban	VOC-limited	Aromatics	[53]
		Rural	VOC-limited	Aromatics
	Pudong	Urban	VOC-limited	Alkenes	[55]
	Xuzhou	Urban	VOC-limited	——
	Yancheng	Urban	VOC-limited	——
	Nantong	Urban	Transition	——
	Dianshan Lake	Suburban	Transition	——
Pearl River Delta region	Tung chung	Suburban	VOC-limited	——	[58]
	Shenzhen	Urban	VOC-limited	Aromatics	[59]
	Heshan	Rural	VOC-limited	Aromatics
	Guangzhou	Urban	VOC-limited	——	[60]
	Huadu	Suburban	NOx-limited	——
	Xinken	Suburban	NOx-limited	——
Sichuan and Chongqing area	Chengdu	Urban	VOC-limited	Aromatics, Alkenes	[53]
	Shuangliu	Urban	VOC-limited	Aromatics
	Pengzhou	Industrial	VOC-limited	Alkenes
	Jinyun Mountain	Suburban	NOx-limited	Alkenes	[61]
Fenhe–Weihe River Plain	Xi’an	Urban	VOC-limited	——	[62]
	Qinling Mountains	Suburban	NOx-limited	——
	Weinan	Urban	Transition	Alkenes	[55]
The junction of Jiangsu-Anhui-Shandong-Henan	Huaibei	Suburban	NOx-limited	OVOCs, Alkanes	[25]
	Dongying	Industrial	NOx-limited	Alkenes, OVOCs	[63]
		Rural	NOx-limited	Alkenes	[64]
	Bozhou	Urban	NOx-limited	OVOCs, Alkenes	This work

) indicates that O₃ production in most urban areas is predominantly VOCs-limited, whereas suburban sites tend to be more sensitive to NO_x emissions or exhibit mixed control regimes.

3.2.2. Photochemical Ozone Formation Budget

Simulation results (Figure 5) depict the production and loss processes of O₃ during the pollution episode. The maximum net O₃ production rate reached 9.6 ppbv/h, with an average daytime (06:00–18:00 LT) production rate of 9.8 ppbv/h and a daily mean of 4.2 ppbv/h. This daily average is slightly higher than that observed at the suburban Huaibei site (4.5 ppbv/h; [25]), but lower than values reported for Nanjing (4.9 ppbv/h; [22]) and Wuhan (6.2 ppbv/h; [65]), and comparable to Chengdu (4.2 ppbv/h; [66]). The O₃ production rate peaks around 11:00 LT before declining sharply, a pattern likely linked to elevated morning NO levels that are subsequently consumed through photochemical reactions. O₃ formation is driven primarily by the reactions of HO₂ + NO and RO₂ + NO, as shown in Figure 2.

The balance between O₃ generation and loss during the pollution episode was illustrated using a stacked plot. Production rates climbed rapidly in the morning, reaching 17.4 ppbv/h near 11:00 LT, before tapering off. By 13:00 LT, production had dropped to 15.4 ppbv/h, coinciding with the highest consumption rate of 10.6 ppbv/h. The magnitude of this production rate is comparable to that reported for Paris, France (15.8 ppbv/h; [67]), but exceeds values observed in Berlin (8 ppbv/h; [68]), London (7.2 ppbv/h; [69]), and San Antonio (3.5 ppbv/h; [70]).

The observed variations highlight the strong influence of precursor emissions and prevailing photochemical conditions, characterized by elevated temperatures, low humidity, and stagnant air masses, on O₃ formation, primarily through peroxy radical (HO₂ and RO₂) chemistry. Model simulations reveal that between 06:00 and 18:00 LT, the HO₂ + NO pathway dominates, with an average reaction rate of 5.4 ± 2.9 ppbv/h, contributing 54.7% of total O₃ production. The RO₂ + NO pathway contributes slightly less, at 4.4 ± 1.3 ppbv/h (45.3%). More than 1000 RO₂ radicals participate in these reactions, but the 12 most reactive species account for 77.9% of the total RO₂ + NO reaction rate (3.5 ± 1.9 ppbv/h). The reaction between CH₃O₂ and NO accounted for the largest share of O₃ production (24.3%), with CH₃CO₃ + NO contributing nearly as much (23.1%). On a daily mean basis, however, HO₂ + NO dominated as the primary pathway driving O₃ generation (Figure 5). However, O₃ removal was controlled mainly by photolysis, responsible for 68.7% of losses, while the reaction of O₃ with NO₂ explained a further 19.1%.

3.3. Atmospheric Oxidation Capacity and Radical Chemistry

To assess the atmospheric oxidizing capacity during the O₃ pollution episode, the F0AM model was applied to quantify the daytime (06:00–18:00 LT) RO_x radical budget, including their sources and sinks. Figure S4 presents the simulated mean diurnal profiles of OH and HO₂ concentrations. The maximum OH concentration reaches 7.53 × 10⁶ molec.cm⁻³, with an average value of 2.69 × 10⁶ molec.cm⁻³, while HO₂ peaks at 1.08 × 10⁹ molec.cm⁻³, with an average of 4.04 × 10⁸ molec.cm⁻³.

The modeled daytime HO_x (OH + HO₂) concentrations in Bozhou are higher than those reported for Heshan in the Pearl River Delta [71] and are comparable to levels in Nanjing, Yangtze River Delta [22], where mean daytime OH and HO₂ were 2.4 × 10⁶ molec.cm⁻³ and 4.7 × 10⁸ molec.cm⁻³, respectively. These results indicate that Bozhou exhibits a relatively strong atmospheric oxidizing capacity. Furthermore, the diurnal cycle of OH closely aligns with that of NO (Figure 2). The OH concentration peaks around midday (~11:00 LT), coinciding with the typical maximum driven by intense solar radiation, highlighting the critical role of photochemistry in enhancing OH production [72].

Photolysis of O₃ represents the dominant source of RO_x radicals, with an average production rate of 0.8 ± 0.7 ppbv/h during daylight hours. This pathway also plays a central role in OH radical formation. The subsequent generation of RO_x is largely sustained through the production of HO₂ and RO₂ radicals. Among these, HO₂ is primarily formed via the photolysis of OVOCs, whereas RO₂ radicals originate mainly from VOC + O₃ reactions and the photolysis of OVOCs.

As illustrated in Figure 6a, O₃ photolysis represents the principal source of primary OH radicals, with a peak rate of 1.8 ppbv/h at approximately 13:00 LT, accounting for 79% of the total primary OH production. HONO photolysis is the second most important contributor, reaching 0.3 ppbv/h (15%) around 08:00 LT. This early-morning peak is likely associated with traffic emissions and the nocturnal buildup of HONO [43].

Regarding radical recycling, the HO₂ + NO reaction is identified as the dominant secondary source of OH, contributing 5.4 ± 2.9 ppbv/h (Figure 7). The primary sinks of OH are reactions with VOCs (2.8 ± 1.6 ppbv/h), CO (2.6 ± 1.9 ppbv/h), and NO₂ (2.4 ± 1.1 ppbv/h). The OH+O₃ reaction constitutes only a minor loss pathway, with a rate of 0.1 ± 0.07 ppbv/h.

Figure 6b shows that HCHO photolysis is the dominant daytime source of HO₂, with an average production rate of 0.63 ± 0.43 ppbv/h. The photolysis of other OVOCs contributes an additional 0.3 ± 0.12 ppbv/h. The OVOC photolysis rate in Bozhou is substantially lower than values reported for major urban environments such as Hong Kong [38] and Beijing [73]. Beyond photolytic processes, reactions of RO₂ + NO (2.4 ± 1.3 ppbv/h) and OH + CO (1.8 ± 0.9 ppbv/h) also constitute important HO₂ sources, as shown in Figure 7. The principal sink of HO₂ is its reaction with NO (5.4 ± 2.9 ppbv/h), followed by self-reaction (HO₂ + HO₂), which occurs at 0.5 ± 0.4 ppbv/h.

In Figure 6c, the photolysis of OVOCs emerges as the dominant source of RO₂ radicals, with an average production rate of 0.2 ± 0.1 ppbv/h, accounting for 66.6% of total primary RO₂ formation. The reaction of unsaturated VOCs with O₃ is the second major contributor, responsible for 19.7% of RO₂ production. The recycling of OH through reactions with VOCs is 5.5 times greater than the combined yield of primary RO₂ sources, underscoring the critical role of radical propagation in sustaining RO₂ levels. The primary sink of RO₂ is the HO₂ + RO₂ reaction, occurring at a rate of 0.7 ± 0.6 ppbv/h, and is largely governed by cross-reactions within the RO_x radical family.

Therefore, the production of RO_x radicals (P(RO_x)) is dominated by photolytic processes. Among these, the photolysis of HCHO, OVOCs, HONO, and H₂O₂ contributes 25.6%, 22.8%, 6.5%, and 1.0% of P(RO_x), respectively. The reaction of NO₃ with VOCs serves only as a minor source, primarily for RO₂ generation. The results highlight that OVOCs, comprising both directly emitted species and secondary carbonyls produced via VOC oxidation, serve as key initiators of atmospheric radical chemistry, exerting strong control over the primary radical budget. Consistently, a recent study in Huaibei City reported that OVOC photolysis accounted for 33% of RO_x production [25].

RO_x radicals are ultimately removed from the atmosphere through deposition processes involving species such as H₂O₂, RONO₂, and ROOH. Throughout the monitoring period, the atmospheric profile exhibited a distinct daily cycle, with NO levels peaking during the morning hours before steadily diminishing as the day progressed. The reported reaction rates of peroxy radicals with NO range from 7.7 × 10⁻¹² to 34 × 10⁻¹² cm³s⁻¹, while their self-reaction rates vary between 5.2 × 10⁻¹² and 37 × 10⁻¹² cm³s⁻¹ [74]. As shown in Figure 7, RO_x termination in the morning is dominated by reactions with NO_x, whereas in the afternoon, self-combination of peroxy radicals becomes the principal sink. Daytime analysis indicates that HO₂ + RO₂, OH + NO₂, HO₂ + HO₂, and RO₂ + NO₂ account for 28.5%, 22.7%, 19.8%, and 12.3% of the total RO_x sinks, respectively. These results are consistent with previous findings showing that in low-NO_x environments, self- and cross-reactions of peroxy radicals dominate termination, leading to substantial production of peroxides (H₂O₂ and ROOH). These peroxides can recycle radicals efficiently, generating OH with yields of up to 80% [75]. This behavior contrasts with high-NO_x regions, where RO_x termination is largely governed by reactions NO_x with (particularly OH + NO₂ and RO₂ + NO) [76]. In the present study, these pathways contributed only 17.1% of the total RO_x sinks, a result consistent with observations in suburban Beijing [73], the Yangtze River Delta [77], suburban Hong Kong [38], and urban Xiamen [78].

Figure 8 presents the average daytime RO_x budget. Radical termination is dominated by cross-reactions among radicals, with HO₂ + HO₂ and HO₂ + RO₂ identified as the principal sinks. In Bozhou, the average daytime loss rates are 0.5 ± 0.4 ppbv/h for HO₂ + HO₂ and 0.7 ± 0.6 ppbv/h for HO₂ + RO₂, while RO_x + NO_x contributes 0.7 ± 0.4 ppbv/h. Compared with Bozhou, the RO_x + NO_x termination rates reported in Changzhou, Hong Kong, and Xiamen are more than twice as high, whereas Bozhou’s rate is more consistent with those observed in Huaibei and Dongying. These differences highlight the sensitivity of O₃ production to NO_x concentrations, underscoring the constraining role of NO_x under VOC-rich conditions. Consistent with observations from other regions, the primary propagation pathway in Bozhou is the conversion of HO₂ to OH. Among these processes, the HO₂ + NO reaction (5.4 ± 2.9 ppbv/h) dominates OH production, exceeding the combined contributions from HONO and O₃ photolysis by more than a factor of five. This finding emphasizes the critical role of NO_x in sustaining atmospheric oxidation capacity. During VOC oxidation, OH radicals are rapidly consumed. Approximately 25.1% of OH reacts with VOCs, producing RO₂ at a rate of 1.8 ± 1.0 ppbv/h, while 38.6% reacts with CO, O₃, or HCHO to generate HO₂ at 2.7 ± 1.5 ppbv/h. The reaction rate of OH with VOCs is nearly six times greater than the total primary production of RO₂, highlighting the strong coupling between OH reactivity and secondary radical formation.

Furthermore, the reaction between RO₂ and NO is the dominant pathway for HO₂ production, contributing 2.4 ± 1.3 ppbv/h. Both RO₂ + NO and HO₂ + NO represent the most rapid propagation processes, facilitating the formation of NO-related RO and OH radicals, along with the byproduct O₃. These propagation pathways clearly govern the overall production of OH, HO₂, and RO₂ radicals, consistent with the results of previous studies (Table S4).

3.4. Sources Apportionment of VOCs

To elucidate the major anthropogenic sources influencing O₃ formation, a PMF model was applied to apportion VOC sources during the O₃ episode. As illustrated in Figure S5, Factor 1 exhibited strong contributions from 2,2,4-trimethylpentane, methylcyclohexane, 2,3-dimethylpentane, and 3-methylhexane, compounds typically associated with industrial processes such as furniture manufacturing, feather product processing, printing, and home furnishings. These chemical profiles are consistent with industrial emissions [79,80]. Factor 2 was dominated by isopentane, a well-established tracer of gasoline evaporation [81,82], representing this source category. Factor 3 was characterized by high isoprene levels. In urban environments, isoprene is primarily of biogenic origin, and this factor was therefore identified as biogenic emissions [83]. Factor 4 included substantial contributions from long-chain alkanes and aromatics, such as n-heptane, 3-methylhexane, 2,3-dimethylpentane, 2,2,4-trimethylpentane, and methylcyclohexane, as well as toluene, ethylbenzene, and xylenes (m/p- and o-xylene). The printing industry is a known source of hexane, heptane, and toluene [84,85], while solvents such as toluene, ethylbenzene, and xylenes are widely used in coatings, paints, synthetic fragrances, adhesives, and cleaning agents [86,87]. Given Bozhou’s substantial number of alcoholic beverage and traditional Chinese medicine packaging printing facilities, this factor was attributed to solvent use emissions. Factor 5 was linked to vehicle exhaust emissions, as indicated by high levels of C₂–C₅ alkanes (e.g., propane, n-pentane, and n-butane), which are characteristic markers of traffic sources [88]. Further, NO_x (introduced as a tracer gas in the model) showed its highest proportion (50%) in this factor, supporting its identification as a vehicular source [89].

Figure 9a illustrates the relative contributions of the five identified VOC sources at Bozhou University, expressed in terms of both concentration and OFP. Based on concentration, vehicle emissions constituted the largest share (28.2%), followed by solvent use (22.6%), gasoline evaporation (19.7%), industrial sources (19.0%), and biogenic emissions (10.5%). When assessed by OFP, vehicle emissions again dominated (27.0%), with solvent use (23.0%), biogenic emissions (17.8%), industrial sources (16.4%), and gasoline evaporation (15.8%) contributing in decreasing order. Taken together, these results indicate that vehicle emissions and solvent use are the primary contributors to O₃ formation in Bozhou.

Figure 9b presents the composition of TVOCs and their respective contributions to OFP at the Bozhou University site. OVOCs represent the largest fraction of TVOCs and are also the dominant contributors to OFP, with acetaldehyde, propionaldehyde, and crotonaldehyde identified as the key species. Alkenes are the second-largest contributors, primarily driven by ethylene, propylene, and 1-butene, while alkanes rank third, with significant contributions from isopentane, n-butane, and propane. These results are consistent with findings in Xi’an [62], where OVOCs accounted for nearly 60% of total OFP.

During O₃ pollution episodes, elevated temperatures and strong ultraviolet radiation can enhance production and emission of BVOCs such as isoprene and oxygenated VOCs from vegetation, thereby strengthening their role in O₃ formation. In addition, elevated temperatures and drought conditions may further promote BVOC emissions (particularly monoterpenes and isoprene), potentially altering O₃ sink pathways; however, this effect cannot be fully assessed in this study because monoterpenes were not measured due to instrumental constraints [90]. Although alkanes are present at relatively high concentrations, their contributions to OFP remain limited due to their comparatively low maximum incremental reactivity (MIR). Aromatic hydrocarbons, despite lower concentrations in Bozhou, generally exhibit higher reactivity and can dominate OFP in regions with extensive solvent use. For instance, in the Pearl River Delta, the proportion of aromatics in OFP has been reported to range from 47 to 65% in Shenzhen [91,92,93] and up to 70% in Guangzhou [94].

4. Conclusions

In this study, the characteristics of O₃ pollution and the VOC composition in Bozhou were comprehensively analyzed. Using the F0AM model coupled with the MCM, the dominant processes driving O₃ formation and removal were identified. O₃ pollution events were found to occur predominantly in June, coinciding with high temperatures and low wind speeds. Among VOCs, OVOCs, alkanes, and halocarbons exhibited the highest concentrations and contributions. The CH₃O₂ + NO reaction was the most significant contributor to local O₃ formation (24.3%), whereas O₃ photolysis represented the dominant removal pathway (68.7%). Sensitivity analysis combined with the EKMA curve further revealed that O₃ formation in Bozhou is NO_x-controlled, and that reducing emissions of OVOCs and alkenes would be particularly effective in mitigating local O₃ levels. Photolysis of OVOCs was also identified as a key driver of radical chemistry, accounting for 33% of RO_x production. The removal of RO_x radicals showed distinct diurnal patterns: in the morning, reactions with NO_x dominated, while in the afternoon, self- and cross-reactions of peroxy radicals, the HO₂ + RO₂ pathway in particular, accounted for 28.5% of radical sinks. Source apportionment further indicated that vehicle emissions, solvent use, and gasoline evaporation were the major anthropogenic contributors during O₃ pollution episodes. However, the role of ethanol emissions, particularly from local beverage industries, could not be assessed in this study due to limitations in ethanol measurement methods. While ethanol is a significant precursor for acetaldehyde, a compound with a major role in O₃ formation, its potential contribution to O₃ production should not be overlooked. Future studies and air quality management strategies should consider the regulation of ethanol emissions, especially from unregulated sources, to fully address O₃ pollution concerns. These findings highlight the critical importance of targeting OVOCs, alkenes, and alkanes in emission control strategies to effectively manage O₃ pollution in Bozhou. Therefore, future air quality management in Bozhou should further reinforce local control measures, with a particular focus on regulating motor vehicle emissions, solvent usage, and gasoline volatilization, while simultaneously restricting urban NO_x emissions. This study reveals that O₃ pollution in Bozhou and other cities at the junction of the JASH provinces is characterized by a NO_x-limited regime, OVOC-dominated reactivity, and dual contributions from traffic and solvent-related sources. These results underscore the necessity of prioritizing NO_x abatement, implementing targeted control of highly reactive VOCs, and enhancing cross-regional collaboration to achieve more effective mitigation of O₃ pollution.