Spatiotemporal Variability of Air Stagnation and its Relation to Summertime Ozone in the Yangtze River Delta of China

This paper investigates the spatiotemporal variability of air stagnation in summer as well as its relation to summer ozone (O3) over the Yangtze River Delta (YRD) region of China. Air stagnation days (ASDs) in the YRD during the summers from 2001 to 2017 range from 9 to 54 days (9.2–58.4% of the entire summer days). With the empirical orthogonal function (EOF) analysis, the dominant weather systems affecting air stagnation in the YRD are illustrated. The first three EOFs explain 68.8, 11.3, and 7.1% of the total variance of ASDs, respectively. The first EOF represents the same phase of the entire YRD, which is attributed to the East Asian summer monsoon and mainly depends on the area and the intensity of the South China Sea subtropical high. The second EOF shows significant maritime-continental contrasts, which is related to stronger near-surface winds on sea. As for the third EOF, the air stagnation in the north and the south of the YRD has the opposite phase, with a dividing line along approximately 31°N. This spatial pattern depends on the area and the intensity of the northern hemisphere polar vortex that affects the meridional circulation. O3 is the typical air pollutant in hot seasons in the YRD. It is generally at a high pollution level in summer, and has a positive trend from 2013 to 2017. Air stagnation can affect O3 pollution levels in the YRD. In ASDs, there are usually weak wind, less precipitation, low relative humidity, high temperature, strong solar radiation and high surface pressure, which are favorable to the formation of O3. More O3 pollution episodes in 2013 than 2015 can be partly attributed to more ASDs in 2013. These results show that stagnant meteorological state can lead to the hazardous air quality, and provide valuable insight into the effect of air stagnation on the changes in surface O3 during hot months.


INTRODUCTION
Air stagnation is usually described as the stable weather condition with less rainfalls and weak winds in the lower to mid troposphere (Garrido-Perez et al., 2018;Li et al., 2019). Weak winds indicate a stable atmospheric stratification with reduced advection and dispersion. Less precipitation means that the wet scavenging process is minimal. It has been revealed that this kind of stagnant weather condition can elevate O 3 or PM 2.5 concentrations, and thereby deteriorate air quality on daily to inter-annual timescales (Wang and Angell, 1999;Jacob and Winner 2009;Horton et al., 2012, Horton et al., 2014Schnell and Prather, 2017;Garrido-Perez et al., 2018. Consequently, air stagnation has significant environmental and health effects (Kerr and Waugh, 2018).
As is well known, China is facing serious air quality deterioration along with the fast economic growth and rapid urban expansion (Chan and Yao, 2008;Ma et al., 2012;Xie et al., 2014;Zhu, 2017;Wu et al., 2020;Hu et al., 2021). In and around the megacities, poor air quality is usually caused by high emissions and adverse meteorological conditions characterized by light wind and less precipitation (Chan and Yao, 2008;Ma et al., 2012;Li et al., 2017;Xie et al., 2017;Xu et al., 2018;Shen et al., 2021;Wang et al., 2021). In recent years, under the very strict emission control strategies implemented by the Chinese government, the effects of meteorological conditions on air pollution have attracted more attention and interest from researchers, especially in the Beijing-Tianjin-Hebei (BTH) region (Xu et al., 2011;Zhang et al., 2016), the Yangtze River Delta (YRD) region (Shu et al., 2016Xie et al., 2016aXie et al., , 2016bGao et al., 2020Gao et al., , 2021Zhan et al., 2020Zhan et al., , 2021, the Pearl River Delta (PRD) region (Xie et al., 2016c;Zhu et al., 2017) and the Sichuan Basin (Zhan et al., 2019;Yang et al., 2020Yang et al., , 2021. Previous investigations have found that air quality can be worse under stagnant weather conditions. Moreover, Huang et al. (2017) revealed that there was a nationwide increasing trend of air stagnation occurrence in China from 1985 to 2014. Li et al. (2019) also reported that urbanization contributed to air stagnation in Shenzhen (a metropolitan city of the PRD). Therefore, how and to what extent air quality deterioration relates to air stagnation need to be further investigated in the city cluster areas of China.
The YRD region is one of the most developed city clusters in the world. It is located in the eastern coast areas of China ( Figure 1A). O 3 pollution is the typical atmospheric environment problem in this region, with a positive trend in O 3 concentration in recent years (Li et al., 2011;Ding et al., 2016;Xu et al., 2018). In previous studies, it was found that high O 3 events generally occur in hot and dry seasons, and are usually related to strong photochemical reactions and high air temperature (Chan and Yao, 2008;Li et al., 2011;Ma et al., 2012;Ding et al., 2013Ding et al., , 2016Xie et al., 2016b;Hu et al., 2016;Pu et al., 2017;Gao et al., 2021;Zhan et al., 2021). The subtropical high also have significant impacts on O 3 concentrations (Shu et al., 2016;Gao et al., 2020;Zhan et al., 2020). Numerous current projections also suggested that O 3 pollution in the YRD is likely to worsen in the future due to the changes in weather conditions, such as the increase of air temperature and the decrease in precipitation Xie et al., 2017), which can increase air stagnation as well. Therefore, it is necessary to study air stagnation and its impacts on summertime O 3 in the YRD. Though some researchers found that air stagnation should not directly used as an index to assess meteorological or climatic effects on air quality without proper assessments, they still pointed out that O 3 pollution and air stagnation can co-occur with greater correlations in some areas (Kerr and Waugh, 2018;Garrido-Perez et al., 2019). Consequently, to study this issue in the YRD can help to evaluate the role of air stagnation in this high polluted region.
The main purpose of this study is to investigate the regional characteristic of air stagnation and its influence on summertime O 3 in the YRD, including 1) the inter-annual variation of air stagnation in summer over the YRD, 2) the dominant weather systems and the corresponding meteorological factors related to air stagnation, 3) the spatiotemporal distribution of summertime O 3 in the YRD and the relations to air stagnation, and 4) the meteorological mechanism of air stagnation impacting O 3 pollution. In the following, the data and the detailed analytical methods used in this study are presented in Data and Methods Section. Results and Discussions Section gives the main findings. A brief summary is shown in Conclusion Section.

Meteorological Data
Air stagnation in the YRD are calculated based on meteorological data from 2001 to 2017. The data include precipitation, 500 hPa winds, 10 m winds, 2 m temperature, relative humidity, surface pressure and solar radiation. As for precipitation, the TRMM 3B42 data (https://pmm.nasa.gov/data-access/downloads/trmm) are used. TRMM 3B42 products are an estimate of precipitation rate based on the combined instrument rain calibration algorithm, with a temporal resolution of 3 h and a spatial resolution of 0.25° (Huffman et al., 2001;Mao and Wu, 2012). These data have been widely used in China in the field of meteorology, hydrology and water resources management (Sun et al., 2012;Zhang et al., 2013). For solar radiation, the monthly data from 2000 to 2017 over China provided by Feng and Wang (2021) are adopted. This dataset has the spatial resolution of 0.1°. It was generated by the geographically weighted regression method to merge the sunshine-duration-derived solar radiation data with the satellite-derived cloud fraction data (MODAL2 M CLD) and aerosol optical depth data (CERES SYN AOD). The data for other meteorological factors are obtained from the daily ERA datasets provided by European Center for Medium-Range Weather Forecasts (ECMWF) (Dee et al., 2011). The datasets have the spatial resolution of 0.25°. They are widely used and have a good application in China as well (Bao and Zhang, 2013;Wang et al., 2015).

Ozone Observation Data
To illustrate the overview of summertime O 3 in the YRD, the air quality monitoring data in the typical YRD cities from 2013 to 2017 are used. The data are acquired from the national air quality real-time publishing platform (http://106. 37.208.233:20035), which provides hourly concentrations of six air pollutants (PM 2.5 , PM 10 , SO 2 , NO 2 , O 3 , and CO) over China. These data are strictly in accordance with the national monitoring regulations. The hourly values for each city are calculated by averaging the concentrations at all national monitoring sites in that city. Identification and handling of invalid and lacking data are also manually performed during data processing, following the methods adopted in some previous studies (Xie et al., 2016b;Shu et al., 2016;Gao et al., 2020Gao et al., , 2021Zhan et al., 2020Zhan et al., , 2021. The YRD region consists of 26 typical cities. As shown in Figure 1B Air Stagnation Day, ASDs, and S n Air stagnation is usually identified by using predefined thresholds of daily upper level winds, near-surface winds and precipitation (Wang and Angell, 1999;Horton et al., 2012;Horton et al., 2014;Huang et al., 2017;Garrido-Perez et al., 2018. In this study, based on the previous researches, the used meteorological variables include wind speed at 500 hPa (as upper level wind), 10 m wind speed (as near-surface wind) and precipitation. Thus, a given day can be considered as an air stagnant day when the daily mean 500 hPa wind speed is weaker than 13 m s −1 , the daily mean 10 m wind speed is weaker than 3.2 m s −1 , and the daily precipitation is less than 1 mm (Wang and Angell, 1999;Horton et al., 2014;Huang et al., 2017). We use ASDs to represent the total number of air stagnation days throughout the summer (June-August).
To study the relation between O 3 pollution and air stagnation (Ozone Pollution and its Relation to Air Stagnation Section), S n is further defined to indicate the air stagnant intensity in a day, given by: where A i denotes the threshold of the ith meteorological variable and B i is the exact daily value of the ith variable. In this study, the value of A 1 for wind speed at 500 hPa is set as 13 m s −1 , A 2 for 10 m wind speed is 3.2 m s −1 , and A 3 for precipitation is 1 mm. The used meteorological data are described in Meteorological Data Section. Large S n represents strong air stagnant intensity. Because the spatial resolutions of the data are 0.25°, the values of ASDs and S n are calculated at each 0.25°grid over the YRD (116-123°E, 27-35°N).

Empirical Orthogonal Function Analysis
The empirical orthogonal function (EOF) analysis has been widely used to split the temporal variance of spatially distributed data into orthogonal spatial patterns called EOFs (Gianelli et al., 2007;Hannachi et al., 2007;Fu et al., 2015). Each EOF has a corresponding eigenvalue, which determines the relative variance contribution to the total variance in the field. Furthermore, the eigenvector, which describes the spatial pattern of the EOFs, is associated with a time series that represents the temporal evolution of that spatial pattern. Most of the variance contribution can be contained into the first few EOFs, which can convey enough information to understand the underlying process. In this study, the NCAR Command Language (NCL) EOF coding package is used. For detailed calculation formulas of EOF as well as the manuals can refer to official website of NCL (https://www.ncl.ucar.edu/Applications/eof.shtml).
To investigate the reasons for the variations of ASDs, the EOFs of ASDs are calculated. Since the time series represent the temporal evolution of its associated spatial pattern, we can effectively obtain the dominant weather systems that affects the spatial pattern by establishing the connection between time series and existing atmospheric circulation indexes (Hannachi et al., 2007;Fu et al., 2015). The atmospheric circulation indexes used in this paper come from 130 climate system monitoring indexes (http://cmdp.ncc-cma.net/ Monitoring/cn_index_130.php) issued by the National Climate Center of China. Based on the meteorological reanalysis data, these historical indexes were calculated and provided monthly. Furthermore, we calculate the linear regression coefficients between the time series and the meteorological variables (500 hPa wind speed, 10 m wind speed and precipitation) defined ASD to investigate the specific mechanism. The regression coefficients are equal to the increment of the variables when the time series change by unit 1.

RESULTS AND DISCUSSIONS
Spatiotemporal Variability of Air Stagnation in Summer Over the YRD Figure 2 gives the spatiotemporal distribution of ASDs in summer over the YRD from 2001 to 2017. The regional average value of summertime ASDs is about 30 days (32.3% of the entire summer days), similarly as found by Huang et al. (2017). There are significant spatial and temporal variations for ASDs. For the inter-annual variation, the regional average value of ASDs ranges from 9 to 54 days (9.2-58.4% of the entire summer days), with the maximum ASDs value in 2010 and the minimum value in 2015. This may be associated with the anomaly of the intensity and position of the western Pacific subtropical high system (discussed in Meteorological Dynamic Mechanism for Air Stagnation Days in Summer of the YRD Section in detail). For the spatial distribution, the values of ASDs on the ocean are usually smaller than those on land for a particular year. In the YRD, ASDs generally show a considerable regional heterogeneity, which is similar with the finding reported by Garrido-Perez et al. (2018) for Europe and Huang et al. (2017) for China.

Meteorological Dynamic Mechanism for Air
Stagnation Days in Summer of the YRD EOF analysis of ASDs is carried out to investigate the above spatiotemporal variations. The first three EOFs explain 68.6, 11.3, and 7.1% of the total variations in ASDs, respectively. Figure 3 shows the results for the first EOF (EOF1). As shown in Figure 3A, the spatial pattern of EOF1 is characterized by the same phase over the entire YRD. Figure 3B further illustrates the atmospheric circulation condition causing this consistency. The time series of EOF1 is correlated with the South China Sea subtropical high area index and the South China Sea subtropical high intensity index, with the correlation coefficients of 0.40 and 0.42, respectively (statistically significant at the 90% confidence level), implying that the consistency over the YRD may depend on the area and the intensity of the South China Sea subtropical high. When the South China Sea subtropical high is large and strong, this spatial pattern is usually typical, which means it is likely to appear air stagnation in the YRD. As the main component of the East Asian summer monsoon, the subtropical high acts on the monsoon anomaly through its location, area and intensity, which can directly affect the summertime precipitation, rain belt distribution, and drought/flood anomalies in eastern China (Ding and Chan, 2005).  coefficients between the time series of EOF1 and the three meteorological variables used to define ASD. The role of each meteorological variable is different in EOF1. Wind speed at 500 hPa ( Figure 3C) and precipitation ( Figure 3E) are the main affecting factors. Generally, with the north jump of the subtropical high, its intensity increases and it controls wide areas of eastern China. In this case, the YRD region is dominated by the subtropical high. The weather is usually stable, and the upper and lower wind fields are generally weak ( Figures 3C,D). In addition, once the subtropical high is northward, the rain belt generated by the cold and the warm air also moves to north, which can result in less precipitation in midsummer of the YRD as well ( Figure 3E). Both weak wind and little precipitation in EOF1 are favorable to cause more air stagnation days. Figure 4 illustrates the results for the second EOF (EOF2). As shown in Figure 4A, the spatial pattern of EOF2 shows significant maritime-continental contrasts, suggesting opposite changes between ocean and land, which can be explained by the fact that the surface wind is usually stronger on sea than on land ( Figure 4D). Figure 4B presents that the time series of EOF2 cannot be linked to existing atmospheric circulation indexes. However, as shown in Figure 4C, it can be found that the north of the YRD is affected by the subtropical jet while the south is affected by the easterlies, corresponding to high wind speeds in the north and low in the south of the YRD at the 500 hPa layer. This may be the factor leading to the spatial pattern of EOF2 on land. Figure 5 presents the results for the third EOF (EOF3). With regard to the spatial pattern, the ASDs in the north and the south of the YRD has the opposite phase, with a dividing line of approximately 31°N ( Figure 5A). Figure 5B shows that the time series of EOF3 has a good relation to the northern hemisphere polar vortex (the tropospheric polar vortex) area index and the northern hemisphere polar vortex intensity index, with the correlation coefficients of −0.42 and −0.42, respectively (statistically significant at the 90% confidence level). When the northern hemisphere polar vortex is small and weak, the north part of the YRD has high ASDs values while the south has low ones. The specific physical process is probably as follows: with the small and weak tropospheric polar vortex, an abnormal highpressure center is prone to occur above the mid-high latitudes of Asia, which is conductive to the weakening of the westerly wind at 500 hPa ( Figure 5C). The atmospheric circulation shows a meridional distribution and the position of the upper-level jet stream is southward. Thus, the cold air can move southward easily, which can form precipitation in the south of the YRD with the warm and wet flow conveyed by the subtropical high ( Figure 5E). For another, the subtropical high is usually strong while the tropospheric polar vortex is weak. The nearsurface wind speed is low in the areas dominated by the subtropical high ( Figure 5B). The tropospheric polar vortex controls the semi-permanent atmospheric center of action, which has important effects on atmospheric circulation at high latitudes. These effects are usually continuous more than seasonal scales. Furthermore, these effects are commonly expressed by significant atmospheric oscillations in climatology, such as the Northern Atlantic Oscillation, the Arctic Oscillation and the East Atlantic-West Russia Pattern (Waugh et al., 2017), which provides a way to link the variances of air stagnation to climate anomalies. As for those cities in the SCR, the MDA8 O 3 almost remains the same, with a small average increment of 0.9 μg m −3 a −1 . The YRD is located in a typical monsoon affected region. The summer monsoon can play an important role in the transport and the dilution processes of O 3 in the YRD. The strong solar radiation and the high air temperature that are related with subtropical high are the main causes of the high O 3 concentration, especially before and after the monsoon rain belt (He et al., 2008;Wang et al., 2011;Zhou et al., 2013;Yin et al., 2019;Jiang et al., 2021). For the low concentration of O 3 in the SCR, it associates with clean maritime airflows from the Pacific Ocean driven by the monsoon (Xie et al., 2016b;Shu et al., 2016).

Ozone Pollution and its Relation to Air Stagnation
To reveal whether air stagnation affects summertime O 3 pollution, Figure 7 illustrates the relationship between air Frontiers in Environmental Science | www.frontiersin.org November 2021 | Volume 9 | Article 783524 stagnation state and O 3 pollution level in the CIR, the NIR, the SCR, and the whole YRD region. The MDA8 O 3 concentrations are divided into three pollution levels from low to high, which are 0-100 μg m −3 (level Ⅰ), 100-160 μg m −3 (level Ⅱ) and higher than 160 μg m −3 (level Ⅲ ). 100 and 160 μg m −3 are the class 1 and 2 criterion for MDA8 O 3 in the National Ambient Air Quality Standard of China, respectively. Moreover, S n defined in Air Stagnation Day, ASDs, and S n Section are used to reflect the stagnant intensity. As shown in Figure 7A, when the O 3 pollution becomes worse, the percentage of S n greater than 0 (tendency to form air stagnation) increases while the percentage of S n less than 0 (tendency to cause the atmosphere unstable) decreases. For the distribution of percentages of the MDA8 O 3 concentrations for a given S n value range, as presented in Figure 7B, the percentage of high O 3 concentration increases with the increasing of S n value, which means more O 3 pollution events occur when the atmosphere is more stable. These findings reveal that the air stagnant status does have an influence on O 3 pollution. It is worth mentioning that the positive relation between O 3 pollution and air stagnation not only occurs in special areas in the YRD (the CIR, the NIR and the SCR) but also is the common phenomena throughout the YRD.
Since the calculation of S n does not cover all meteorological factors that affect O 3 concentrations, it is necessary to discuss the performance of other meteorological factors in air stagnation days. Figure 7C gives the distribution of meteorological factors for a given S n value range. The meteorological factors include relative humidity (RH), 2 m air temperature (Temp) and surface air pressure (SP). As illustrated in Figure 7C, the days with S n greater than 0 (tendency to form air stagnation) usually have lower relative humidity, higher 2 m temperature and higher surface pressure than days with S n less than 0 (tendency to cause the atmosphere unstable) in the YRD. Low relative humidity and high temperature, as well as less precipitation that results in more solar radiation to penetrate the atmosphere, are all favorable to form O 3 pollution episodes (Ding et al., , 2016Pu et al., 2017). Particularly, the 2 m temperature increases with the S n value, which explains that the high O 3 pollution level tends to occur when S n is greater than 1 (the atmosphere is more stagnant).

Mechanism for the Effect of Air Stagnation on O 3 Pollution in the Summer of 2013 and 2015
Previous studies, as well as the result of Spatiotemporal Distribution of O 3 Section, show a positive trend of O 3 concentrations in the YRD during 2013-2017 Wang et al., 2020;Zhan et al., 2021). However, the O 3 pollution  Figure 8 shows the summertime averages and the differences between 2013 and 2015 for the three meteorological variables identifying air stagnation day. In the 500 hPa weather map of 2013 ( Figure 8A), the tropospheric polar vortex is large and strong. The flat isopleths indicate that there is a small geopotential height gradient, which can result in weak wind in the YRD. However, in 2015, the tropospheric polar vortex is small and weak. There are obvious troughs and ridges in the upper reaches of the YRD ( Figure 8B), and thereby the cold air can move southward. These differences are visually shown in Figure 8C. Compared to 2015, there is a significant positive potential height perturbation in 2013, which can lead to easterly wind component over the YRD and result in a smaller wind speed at 500 hPa atmospheric layer. Furthermore, the westerly component appearing at 45°N confirms the fact that the westerly jet lies more to the north. For 10 m wind speed, it is higher on the ocean than on the land in both 2013 ( Figure 8D) and 2015 ( Figure 8E), which partly explains the reason why the ocean usually has a smaller ASDs. Figure 8F shows that the 10 m wind speed has a southwest component in 2013 (compared with 2015), which can block the prevailing southeasterly wind.
As for precipitation, there is a significant difference in the spatial distribution between 2013 and 2015. In the summer of 2013, there are more rainfalls in the south of China, and there is less precipitation in the YRD and the north part of China ( Figure 8G). In the summer of 2015, however, more rains fall in the YRD, especially in the south of Anhui province ( Figure 8H). The difference of precipitation between 2013 and 2015 (precipitation in the summer of 2013 minus that in 2015) are shown in Figure 8I. Obviously, the precipitation over the YRD is much higher in 2015, implying that the processes of the dilution and the removal of air pollutants are more intensive in 2015. Less precipitation in 2013 also means there are more intensive solar radiation reaching the Frontiers in Environmental Science | www.frontiersin.org November 2021 | Volume 9 | Article 783524 ground and higher air temperature near the surface over the YRD, as shown in Figure 9.
In summary, larger and stronger of the tropospheric polar vortex and the subtropical high result in more air stagnation days over the YRD in the summer of 2013. Under this circumstance, the upper-and lower-level winds are weak, and more air pollutants including O 3 and its precursors are trapped near surface over the YRD. Moreover, less precipitation, higher air temperature and stronger solar radiation that are associated with air stagnation facilitate the photochemical reactions of O 3 formation. Then, more O 3 pollution days occur in the summer of 2013. The weather systems and the changes in relevant meteorological factors related to air stagnation can affect the physical and chemical processes of O 3 formation, and thereby severe O 3 pollution tends to form under air stagnant conditions.

CONCLUSION
Stagnant meteorological state can lead to hazardous air quality. O 3 is the typical air pollutant in hot seasons of the YRD. In this study, air stagnation and its impact on summertime O 3 in the YRD are investigated. The summertime air stagnation days over the YRD have significant spatiotemporal variations from 2001 to 2017. The regional average value is about 30 days (32.3% of the entire summer days) in the YRD. The values range from 9 days (9.2%) in 2015 to 54 days (58.4%) in 2010. The values on the ocean are usually smaller than those on land. Based on EOF analysis, the first three EOFs explain 68.8, 11.3, and 7.1% of the variations of air stagnation days in the YRD, respectively. The spatial pattern of the first EOF is related to the East Asian summer monsoon, and mainly depends on the area and the intensity of the South China Sea subtropical high. When the South China Sea subtropical high is large and strong, air stagnation is likely to appear in the YRD. The second EOF shows significant maritimecontinental contrasts, which is due to stronger surface wind on sea than that on land. As for the third EOF, the north and the south of the YRD has the opposite phase, with a dividing line along approximately 31°N. This spatial pattern is related to the area and the intensity of the northern hemisphere polar vortex that can affect the meridional circulation. When the northern hemisphere polar vortex is small and weak, the north part of the YRD has more air stagnation days. O 3 concentration is high in summer and shows an increase from 2013 to 2017 over the YRD. The 26 typical YRD cities can be classified into three categories (CIR, NIR, and SCR) based on their O 3 characteristics and geographical locations. The cities in the CIR have the highest concentrations of MDA8 O 3 . The cities in the NIR have the most rapid increasing of MDA8 O 3 . Air stagnation can affect O 3 pollution levels in the YRD. The percentage of high O 3 pollution level increases with air stagnant intensity both in special areas and all over the YRD. Weak wind, less precipitation, low relative humidity, high temperature, strong solar radiation and high surface pressure under stagnant days are favorable to form severe O 3 pollution. More stagnant weather condition in 2013 can explain more O 3 pollution episodes in that year than in 2015. Larger and stronger of the tropospheric polar vortex and the subtropical high result in more air stagnation days over the YRD in the summer of 2013. Under this circumstance, there are weaker upper-and lower-level winds, less precipitation, higher air temperature and stronger solar radiation over the YRD in 2013 than 2015. The weather systems and the changes in relevant meteorological factors can affect the physical and chemical processes of O 3 formation, and thereby severe O 3 pollution tends to form.  This work provides an overview of air stagnation and its behaviors over the YRD, and discusses its effects on the summertime O 3 pollution over this region in recent years. The above findings provide valuable insight into the formation of O 3 pollution in the YRD, and help to understand the effect of air stagnant state on the changes in surface O 3 concentration in hot seasons.

DATA AVAILABILITY STATEMENT
The original contributions presented in the study are included in the article/supplementary material, further inquiries can be directed to the corresponding author.

AUTHOR CONTRIBUTIONS
MX had the original ideas, designed the research, collected the data, prepared the original draft, and acquired financial support for the project leading to this publication. CZ carried out the data analysis and helped to prepare the original draft. YZ, JS, and YL help to collect the data and prepare the original draft. MZ, QL, and FS reviewed the initial draft and checked the English of the original manuscript.