Special Issue on COVID-19 Aerosol Drivers, Impacts and Mitigation (XVII)

Ying LThis email address is being protected from spambots. You need JavaScript enabled to view it.1,2 , Haoxiang Xu1 

1 Department of Ocean Science and Engineering, Southern University of Science and Technology, Shenzhen, China
2 Center for Oceanic and Atmospheric Science at SUSTech (COAST), Southern University of Science and Technology, Shenzhen, China

Received: November 24, 2020
Revised: February 12, 2021
Accepted: May 20, 2021

 Copyright The Author(s). This is an open access article distributed under the terms of the Creative Commons Attribution License (CC BY 4.0), which permits unrestricted use, distribution, and reproduction in any medium, provided the original author and source are cited.

Download Citation: ||https://doi.org/10.4209/aaqr.200644  

Cite this article:

Li, Y., Xu, H. (2021). Assessment of Reductions in Emission-driven Air Pollution during the Beijing Olympic Games, Shanghai World Expo, Guangzhou Asian Games and Wuhan COVID-19 Lockdown. Aerosol Air Qual. Res. 21, 200644. https://doi.org/10.4209/aaqr.200644


  • Emission-driven (ED) factor generally played a much stronger role in all the events.
  • ED effectiveness for air quality improvement of COVID-19 is not as large as expected.
  • Meteorology-driven (MD) effect worsened the air quality during Shanghai Expo event.
  • MD effect improves air quality in Wuhan, Beijing and Guangzhou events.
  • Strategies are less effective for reducing urban NO2 and not work for O3 reduction.


Quantifying and comparing the effectiveness of different emission control strategies can provide insights for policy design and air quality management. In our previous work, we developed a wind-pollution decomposition (WPD) method that provides a robust tool to quantify meteorology-driven and emission-driven impacts on changes in air quality. In this study, we applied this method to quantify emission-driven impacts on the observed air quality changes during the three largest international socioeconomic mega-events in China, namely, Shanghai World Expo in 2010, Beijing Olympic Games in 2008, and Guangzhou Asian Games in 2010. We also applied the method to the air quality variation during the lockdown period in Wuhan due to COVID-19 and compared the emission-driven impacts on air quality among these events. The results quantitatively show that the emission-driven factor generally played a much stronger role (> 86%); the meteorology-driven factor promoted pollution mitigation during Wuhan, Beijing and Guangzhou events but worsened the air quality during Shanghai event. The emission-driven pollution reduction was largest in the Wuhan COVID-19 lockdown (64% NO2, 54% PM2.5 reductions), followed by Beijing Olympics (42% PM2.5, 31% NO2 reductions), The Wuhan COVID-19 impact on air quality improvement is not as effective as expected especially for O3, which implies the difficulty of air quality attainment under normal, non-lockdown daysComparison of these events show that shutdown or emission control measures applied to industries and power plants were generally benefit for PM2.5, SO2 and NO2 reduction, while those applied to on-road traffic control are less-effective for reducing NO2 and not works for the mean O3 reduction. The results imply that advanced control measures for vehicle exhaust and control strategies considering the interaction between O3 and NOx/VOC/PM are necessary. In addition, the ongoing supervision of control strategies implementation is one of the key issues for future air quality management in China.

Keywords: Emission controls, Effectiveness, Mega-events, PM10, O3


The haze and photochemical smog events that have occurred frequently since 2010 in the key city clusters of China, such as, the Yangtze River Delta (YRD), the Pearl River Delta (PRD) and Jing-Jin-Ji (JJJ), indicate a significant regional air quality issue in China. To improve air quality and protect public health, different administrative levels of government have implemented a range of intervention programmes to reduce anthropogenic emissions. In the Action Plan for Air Pollution Prevention and Control (i.e., the ‘National Ten Measures’) (MEP, 2013), instead of targeting reductions in emission amounts, the Chinese government targeted direct reductions in air pollution concentrations, especially for the three most polluted regions, JJJ, YRD and PRD.

To adjust policy recommendations in time, the effectiveness of policies for controlling ambient air quality must be assessed within a relatively short period (e.g., at the inter-annual scale). In China, government agencies report the national air quality annually or semi-annually to review the success or failure of the related efforts. Therefore, it is of interest to investigate the impacts of implemented control strategies on air quality at the same time scale. However, the impact of emission control is generally difficult to quantify at this scale since the impact is often intertwined with the impact of pollution transported via meteorological factors. The impacts of regional or superregional pollution transport, as well as those of local emission dispersion, are all subject to ambient wind conditions, which change significantly at the synoptic scale and notably at the inter-annual scale (Katsoulis, 1988; Wang et al., 1998; Chung et al., 1999; Lo et al., 2006; Gietl and Klemm, 2009; Li et al., 2012a). For example, in a year, the higher frequency of weak wind will lead to a deterioration of air quality even though there is no emission increase compared to the previous year (Lo et al., 2006; Gietl and Klemm, 2009).

In general, without aggressive intervention control programmes, the separation and evaluation of emission-driven and meteorology-driven changes in inter-annual air quality is very difficult, since the change in air quality due to emission-driven impacts could be small and difficult to differentiate from the changes caused by other impacting factors. However, during mega-events in China that employed aggressive intervention strategies for periods of several months to control emissions, emission-driven factors likely made the dominant contribution to air quality improvement. In addition to the COVID-19 lockdown period in Wuhan, which resulted in significant emission reductions, the Beijing Olympic Games in 2008, the Shanghai World Expo in 2010, and the Guangzhou Asian Games in 2010 are the three largest international socioeconomic mega-events in China that have resulted in lasting aggressive emission abatement (Lin et al., 2013a); these events represent good opportunities to evaluate the emission-driven and meteorology-driven impacts on air quality changes, and to assess the effectiveness of different control strategies applied. Notable air quality improvement was reported for the Beijing Olympic Games (Wang et al., 2009a; Mijling et al., 2009; Wang et al., 2009c; Chen et al., 2013; Gao et al., 2013; Li et al., 2013a; Wang et al., 2013; Wang et al., 2014; Liu et al., 2015a; Liu et al., 2015b; Yang et al., 2015; Norra et al., 2016), the Shanghai World Expo (Fu et al., 2011; Hao et al., 2011; Huang et al., 2012; Cheng et al., 2013; Huang et al., 2013; Lin et al., 2013b), and the Guangzhou Asian Games (Li et al., 2012b; Liu et al., 2013; Xu et al., 2013; Yao et al., 2013; Lin et al., 2014; Tao et al., 2015). Significant variation in pollution levels (61%, 25%, 20%, and 21% for daytime SO2, CO, O3, and NOx reduction, respectively) were observed in August 2008 compared to August 2006–2007 in the Beijing urban area (Wang et al., 2009b). For the Shanghai Expo, the daily average concentrations of PM10, SO2 and NO2 decreased by 25.0%, 10.9% and 18.1%, respectively, compared with those in the same period in 2009 (Fu et al., 2011). Reductions of 12.84%, 8.84%, 28.17% and 23.31% were observed for NO2, O3, PM10, and SO2, respectively, during the Asian Games period (Li et al., 2012b). In addition, the COVID-19 lockdown in Wuhan city in 2020 also provides an opportunity to easily validate the results of differentiating emission-driven changes from meteorology-driven changes in air quality. Due to the rapid outbreak of COVID-19, the megacity of Wuhan, which has a population of more than ten million, underwent a lockdown that lasted for 76 days. The Wuhan lockdown led to a substantial reduction in economic damage and local emissions during the lockdown period (Bherwani et al., 2020; Le et al., 2020). To quantify the emission-driven effect on air pollution reduction during the four events, it is necessary to separate the meteorology-driven effect from the air quality variation. Some studies have reported the emission-driven effect for a specific event and identified the emission-driven contribution. However, most of these results are dependent on complex subjective data analysis for a specific case or unconventional observations (Huang et al., 2013), and it is difficult to quantitatively acquire and compare the emission-driven contributions for the different events; nonetheless, such assessment and comparisons of different events have crucial environmental policy implications for mitigating air pollution and benefitting public health.

In our previous work (Li et al., 2014), we developed a wind-pollution decomposition method (WPD) that provides an objective and effective tool to quantify meteorology-driven and emission-driven impacts on air quality changes at the inter-annual scale and that does not depend on the subjective parameter selection or emission factor construction. In this study, we used this WPD method to quantify the effectiveness of the integrated control programmes implemented in the three largest international social events in China and the passive emission reduction due to the COVID-19 event in Wuhan. The emission-driven and meteorology-driven impacts on the observed air quality changes during these events were quantified and compared based on the best available observational data. Based on the quantified results with this objective and robust method, we first compare the control effectiveness of the different mega-events together. The remainder of this paper is organized as follows. In Sect. 2, we describe the observational dataset and the methodology used in the analysis. In Sect. 3, we present and discuss the decomposition results for the Beijing Olympic Games in 2008, the Shanghai World Expo in 2010, the Guangzhou Asian Games in 2010 and the COVID-19 event in 2020. In the conclusion section, we summarize the results.


Beijing hosted the Summer Olympic Games from 8 to 24 August, 2008, and hosted the Paralympic Games from 9 to 17 September, 2008; these events were the first and largest international mega-event in China at that time. The national government made a first attempt to improve the air quality during this period by carrying out a series of intervention programmes, such as closing or relocating industrial plants, decreasing local power generation, suspending construction, promoting natural gas usage, implementing strict traffic restrictions, and other interventions. The Shanghai World Expo was held from 1 May to 31 October 2010. It is the longest international event ever held in China. In total, 73 million visitors attended this mega-event. Shanghai is located at the eastern tip of the YRD, which is made up of the largest contiguous metropolitan areas in the world. The YRD region comprises the megacity of Shanghai and many other cities in Jiangsu and Zhejiang provinces; it is also one of the most industrial regions in China, contributing approximately 21.4% of the national gross domestic product (GDP) (UNEP, 2009). Guangzhou hosted the Asian Games from 12 to 27 November 2010, and the Asian Para Games from 12 to 19 December 2010. Guangzhou is located at the center of the PRD, which is one of the most rapidly developing regions in China. The area included Guangzhou, Hong Kong, Macau, and 8 other cities is called the PRD economic zone (PREZ). The PREZ is one of China’s leading economic regions and a major manufacturing center. A total of 4.2% of the total Chinese population live in the PREZ, and the PREZ generates 9.3% of the GDP in China. It is the largest urban area in the world (World Bank, 2015). COVID-19, officially called coronavirus disease 2019, initially broke out in the city of Wuhan, China, in December 2019 and appeared all around the world in the next year. Due to the severity of the outbreak, the Chinese government decided to temporarily quarantine Wuhan city to prevent the spread of the disease. During the lockdown period, only production activities that were closely related to residents’ basic living requirements, such as vegetable processing, were allowed to continue. The lockdown began from 23 January, ended on 8 April 2020. According to an announcement from the national government, factories and enterprises were not allowed to return to production until 21 March. Therefore, this strict lockdown created a unique 58-day period in which pollutant emissions should be very low. Meteorology data was from the closest Global Telecommunications System (GTS) stations. Hourly air pollution data was taken from national air quality monitoring stations. Due to limitations on data availability, we do not have every pollutants for all the events. The data available for this work are summarized in Table S1. Detailed data information for individual events and geographical position are also provided in the Supporting Information (SI).

With the WPD method, we can decompose the mean variation in pollutant concentrations between two periods into a wind contribution (representing the meteorology-driven contribution), a non-wind contribution (representing the emission-driven contribution), and a non-linear term. In this method, a linear index L is defined and validated by the Monte Carlo method to show the relative importance of each linearly decomposed contribution. A result with L > 0.87 is considered significant at a 90% confidence level. The decomposition analysis is only applied for the cases if the expectation value of the concentration average is within 5% difference compared to the average value calculated based on the original time series. Before the analysis, we also carried out following checking steps to avoid impact of data contamination. (1) Remove uncompleted data in group (e.g., if data of wind direction missed, data of wind speed and pollutant will not be induced into the decomposition analysis); (2) exclude inconsistent data (for example, pollutant concentration suddenly drop to zero); (3) exclude data from specific station that has too many missing (or in-consequent) data. The details of the method can be referred to Li et al. (2014). We also specify the key principles of the decomposition method in the Supporting Information (SI) in order to provide a self-contained study. The uncertainties of applying wind to represent meteorology, and non-wind to represent emission-driven is limited in these events and discussed in Sect. 4.


3.1 Analysis for 2010 Shanghai World Expo

We first present the analysis for the Expo event as an example to show clearly how WPD can be applied to analyze and evaluate the effectiveness of control programs on air quality. The WPD analysis method was applied to decompose the pollution variation between the mean pollutant concentration values during the Expo period (1 May–30 November) of 2010 (control period) compared to the same period of 2009 (pre-control period). Several air quality stations were selected to represent air pollution in Shanghai (see Fig. S1): PuDong station (PD) located in the east of urban area; DianShan Lake station (DSL) located at the southwest boundary of Shanghai; and a city average which is the mean concentration of other stations.

Wind Roses and PM10 Pollution Rose Pattern Analysis: The wind roses (Figs. 1(a) and 1(b)) show that the winds are dominated by southeasterly in both 2009 and 2010. The change in the wind roses from 2009 to 2010 (Fig. 1(c)) shows more southeasterly while less others in 2010. The pollution roses (Figs. 1(d) and 1(e)) show that there is higher pollution levels from the northwest and southwest side and lower pollution level from the eastern side, which indicates the polluted air mass transport from the western China Central Plain (Huang et al., 2012; Lin et al., 2013b) and the cleaner air mass brought by the easterly from the sea. Pollution Rose can clearly show the direction of the impacting source to the receptor station by transport, while it is hard to quantitatively identify the source distance by wind speed. But generally speaking, the weak winds are more relevant to local/regional emission effect, while the wind with high speed can bring the regional/super-regional pollutants. Compared with pollution rose of 2009 (Fig. 1(d)), the pollution rose difference is shown in Fig. 1(f). The pollution concentration of 2010 decrease significantly in northwest direction almost in all wind speeds, which indicates a reduced emission contribution of the regional and even super-regional transport from northwest; in southwest direction, the pollution concentration of 2010 decreased with low to middle wind speed, and increased with relatively high wind speed (Fig. 1(e)), which indicates an emission reduction in local and regional sources, but an increased emission contribution by long-term transport from southwestern side. In addition, the PM10 concentration is much lower in low wind speed (less than 2m s-1) than those in higher wind speed in 2010, which indicate a greater effort from local emission control than that in non-local areas in 2010.

Fig. 1. Wind and PM10 pollution roses at DSL of Shanghai (up direction as north): (a) wind rose of 2009; (b) wind rose of 2010; (c) change in wind rose from 2009 to 2010, (d) pollution rose of 2009 (unit: µg m–3), (e) pollution rose of 2010 (unit: µg m–3), (f) change in pollution rose from 2009 to 2010 (unit: µg m–3), (g) wind effect (unit: µg m–3); (h) non-wind effect (unit: µg m–3). The wind rose shows the normalized frequency distribution of wind as a function of speed and direction; pollution rose shows the corresponding average pollutant concentration as a function of wind speed and direction of individual groupings. The small circle represents the 2 m s–1 wind speed and the large circle represents the 8 m s–1 wind speed.Fig. 1. Wind and PM10 pollution roses at DSL of Shanghai (up direction as north): (a) wind rose of 2009; (b) wind rose of 2010; (c) change in wind rose from 2009 to 2010, (d) pollution rose of 2009 (unit: µg m–3), (e) pollution rose of 2010 (unit: µg m–3), (f) change in pollution rose from 2009 to 2010 (unit: µg m–3), (g) wind effect (unit: µg m–3); (h) non-wind effect (unit: µg m–3). The wind rose shows the normalized frequency distribution of wind as a function of speed and direction; pollution rose shows the corresponding average pollutant concentration as a function of wind speed and direction of individual groupings. The small circle represents the 2 m s–1 wind speed and the large circle represents the 8 m s–1 wind speed.

Emission-driven Effect of PM Pollutant: the non-wind effect on PM10 concentrations (Fig. 1(h)) during the Expo event can be estimated from the spatial product of the wind rose of 2009 (Fig. 1(a)) and the difference between the pollution roses (Fig. 1(f)). Fig. 1(h) shows that the pollution concentration (emission contribution) was reduced in most directions especially from the western side to Shanghai during the Expo event. This result is the expected result of the air quality control strategies implemented for the Expo event, which included the fugitive dust control measures, reductions in coal burning at power plants, the closure of highly polluting factories and strict emission standards for vehicles (Huang et al., 2012). However, we also found an unexpected increase in pollution to the southeast at low to moderate wind speeds, which indicates that there was an unexpected increase in PM10 emissions from the south-eastern part of Shanghai (Feng Xian district) or there was an unexpected increase in PM10 emissions from the south-western area of Shanghai and the neighboring rural area of Zhejiang Province, where are relatively undeveloped areas that produced mainly agricultural emissions and very limited chemical industrial emissions before 2011. Huang et al. (2013) reported an increase in open biomass burning in the summer and autumn of 2010 (compared to that in 2009) on the south-eastern Shanghai and/or northern Zhejiang Province, where widespread fire spots with MODIS was detected in these regions; and high correlation between PM2.5 and K+, a typical tracer for biomass burning, was found during the biomass burning episodes; they consequently point out the ineffective control strategies of biomass emission during the Expo. Considering the derived biomass burning impact in Huang et al.’s (2013) study, we believe that the unexpected increase in non-wind PM10 pollution in the SE and SW direction reflects a failure to completely control biomass burning emissions from south-western Shanghai and northern Zhejiang Province, although the ban of open biomass burning issued was a regional-joint statute by the Shanghai, Jiangsu, and Zhejiang governments during the Expo period. This result shows that the ongoing supervision of control strategies is important for air quality management. Meanwhile, this case is an excellent example of the strength of this WPD method for capturing changes in integrated emissions using only routine air quality and meteorological data, which are easily obtained from open sources (e.g., national air quality monitoring networks and global telecommunications systems).

To explore the relative contributions of the wind and non-wind factors, the percentages of wind, non-wind and non-linear effects relative to the changes in PM10, SO2, and NO2 concentrations and the linear index (L index) for the expo period were then calculated and are provided in Table 1. As shown in Table 1, during the Expo period, the non-wind effect was the dominant factor in pollution mitigation during the Expo period (85% to 146%), except for NO2 pollution at the PD station (116%); the wind contribution was very small (1% to 24%) and was even a factor aggravating the SO2 and NO2 pollution at the DSL station (13% and 5%). These results indicate the success of control strategies to reduce PM10 and SO2 concentrations and the failure of urban NO2 control strategies.

Table 1. The decomposition result in Shanghai during the Expo period (compared with the corresponding time period of the previous year).

Effectiveness of the Stationary and Mobile Source Control: The SO2 and NO2 pollution roses at the same urban station in Shanghai in 2009 and 2010 are plotted in Figs. 2(a)–(c) and Figs. 2(d)–2(f), respectively. By comparing Fig. 1(f) with Figs. 2(c) and 2(f) we have: the SO2 concentration had a more uniform decreasing pattern than the PM10 from 2009 to 2010, while the mean concentration of NO2 was dominated by an overall increasing pattern. The above pollution rose’s difference between 2010 and 2009 indicates the control policies for PM10 and SO2 is effective but ineffective for NO2. This result is consistent with the study of Lin et al. (2013b), which reported that Shanghai experienced low SO2 and PM10 levels but high NO2 and O3 levels during the Expo period. An increase in NO2 (2.5 ppb) was observed at the PD station. The decomposition results show that the increase in NO2 was 116% dominated by non-wind factors, which indicates even an increase in NO2 emissions in urban areas.

Fig. 2. Pollution roses at rural site of Shanghai (a) SO2 of 2009 (unit: ppb), (b) SO2 of 2010 (unit: ppb), (c) SO2 difference of 2010–2009 (unit: ppb); (d) NO2 of 2009 (unit: ppb), (e) NO2 of 2010 (unit: ppb), (f) NO2 difference of 2010–2009 (unit: ppb); (g) SO2/NO2 of 2009 (unitless), (h) SO2/NO2 of 2010 (unitless), (i) SO2/NO2 difference of 2010–2009 (unitless); The small circle represents the 2 m s–1 wind speed and the large circle represents the 8 m s–1 wind speed.Fig. 2. Pollution roses at rural site of Shanghai (a) SO2 of 2009 (unit: ppb), (b) SO2 of 2010 (unit: ppb), (c) SO2 difference of 2010–2009 (unit: ppb); (d) NO2 of 2009 (unit: ppb), (e) NO2 of 2010 (unit: ppb), (f) NO2 difference of 2010–2009 (unit: ppb); (g) SO2/NO2 of 2009 (unitless), (h) SO2/NO2 of 2010 (unitless), (i) SO2/NO2 difference of 2010–2009 (unitless); The small circle represents the 2 m s–1 wind speed and the large circle represents the 8 m s–1 wind speed.

To investigate the cause of the failure control of urban NO2, we further apply the WPD on the ratio of SO2 to NO2, as an indicator to reflect the impact of stationary sources relative to that of mobile sources (Nirel and Dayan, 2001). Nirel and Dayan found that the ratio of SO2/NO2 had a typical relationship along mobile source. It should be applicable in this case because the urban NO2 emission mainly released from the stationary source and on-road mobile sources, while SO2 emission is mainly from stationary source during Expo. For the stationary source, in order to accomplish the environment protection goal of the Eleventh Five-Year Plan (MEP, 2006), flue-gas desulfurization (FGD) control for SO2 and selective catalytic/non-catalytic reduction (SCR/SNCR) control for NO2 were widely installed on stationary source, which generally have a similar effectiveness in pollution removal ratio (> 80%, MEP, 2005, 2010). Thus, the SO2/NO2 (SO2_stationary/(NO2_mobile + NO2_stationary)) ratio should be more sensitive to the relative effectiveness of mobile source control. The pollution roses for the SO2/NO2 ratio at the same station in Shanghai for 2009 and 2010 are plotted in Figs. 2(g)–2(i)). The SO2/NO2 ratio at a moderate to high wind speeds was generally higher than 1.2 in 2009 (Fig. 2(g)), indicating more SO2 than NO2 came from regional or super-regional transport. The SO2/NO2 ratio at almost all speeds and directions decreased to below 1 in 2010 (Fig. 2(h)), which indicates stronger control of SO2 emissions from stationary sources than of NOx emissions from mobile sources both in the local and regional areas. The analysis results for NO2 and the SO2/NO2 ratio suggest that the increase in NO2 from non-wind factors possibly due to the ineffective mobile emission control. This failure control is also supported by Lin et al. (2013b). They found a NO2 had higher correlations with PM2.5 than SO2, indicating mobile source contributed a lot to local NO2 emission. Huang et al. (2013) also showed that the stationary source in Shanghai had less contribution to heavy NO2 and CO pollution; organic matter and black carbon contributed a lot to PM1 (Huang et al., 2012), which closely related to vehicular emission. NO2 control during the Expo period may have failed: though the emission standard for on-road traffic was updated before the Expo, no actions such as those taken for Beijing Olympics were taken for NO2 control. Therefore, the uncontrolled traffic emissions and the tremendous number of visitors to the Expo are likely the reasons for the increase in NOx emissions at urban areas during the Shanghai Expo.

3.2 Analysis for 2008 Beijing Olympics

In this section, we used the WPD method to quantify the meteorology-driven and emission-driven impacts on changes in pollution concentrations in Beijing during the period of the Olympics (1 July–31 August) in 2008 compared with the corresponding period in 2007. Although limited data were available for the Beijing Olympics event, we were still able to quantify the PM and NOx trends. Hourly NOx and PM2.5 measurements taken at the Peking University station. Table 2 shows the decomposition results. Mean concentration for all pollutants during the Olympic period in 2008 are lower than the corresponding period in 2007. In particular, reduced concentrations of NOx (13.02 ppb) and PM2.5 (59.13 µg m–3) are excellent. The confidence level (the linear index C-L) for all pollutants are equal to 0.99, indicating our confidence in the results (i.e., the linear decomposition results did not happen by chance for 99% possibility). According to the results, both meteorology-driven and emission-driven effects contributed to air quality improvement during the Olympics. Specifically, the emission-driven effect contributed as much as 86% and 94% of the NOx and PM2.5 concentration reductions respectively, while meteorology effect contributed approximately 16% and 4% respectively.

Table 2. The decomposition result of primary pollutants in Beijing for the Olympic period (July 1–August 31) in 2008 compared with the corresponding time in 2007.

The significant emission-driven contribution to the reduction in PM2.5 pollution (59.13 × 94% = 55.58 µg m–3) suggests an effective control during the Beijing Olympics. Various measures were taken to reduce emissions, including closing or relocating industrial plants, decreasing local power generation, suspending construction, promoting natural gas usage, and implementing strict traffic (e.g., the odd/even license plate number rule was applied to personal vehicles in Beijing). The can be derived with itself in concentration format (Non-wind effect × ΔC) divided by mean concentration of the same period in 2007 (C1), which is 42% for PM2.5 and 31% for NO2. These coincide well with other numerical simulation studies. Gao et al. (2011) used WRF-Chem to investigate the effectiveness of government control during Olympics. Their result shows a 43% emission-driven reduction for PM2.5. Xing et al. (2011) also applied a WRF-CMAQ model to simulate the emission control impact during Olympics. Result shows a 16–48% emission-driven reduction for PM2.5 and a 16–32% reduction for NO2 in urban area. Those results demonstrate Beijing had an effective emission control during the Olympics and emission-driven cleaning is dominating effect on air quality improvement.

However, PM10 and PM2.5 exceeding were still recorded by Wang et al. (2010) for many days during the Olympics, despite the aggressive emission restrictions were implemented via a JJJ regional-joint control regardless of economic losses. This outcome reveal a substantial challenge of meeting air quality standards in Beijing and the JJJ region, due to the high national background of PM2.5. The average PM2.5 concentration in Beijing was 42 µg m–3 in 2019, much lower than the PM2.5 concentration during the Olympics (72.58 µg m–3) and its corresponding period in 2007 (131.71 µg m–3). Up to now, a great success has been achieved by PM emission control, resulting a more environmental-friendly society that catch up with the Eleventh Five-Year Plan (MEP, 2006).

3.3 Analysis for 2010 Guangzhou Asian Games

For the Guangzhou Asian Games, the WPD analysis was performed on SO2, NO2, and PM10 pollution at Luhu station for the period of 1 October to 31 December in 2009 and 2010. The quantification results are provided in Table 3. The confidence level of all decomposition results is higher than 90%. During the Asian Games, seven major air pollution control measures were carried out in Guangzhou and nearby cities: limiting emissions from thermal power plants, supervising heavily polluting factories, implementing traffic restrictions, restricting marine vessel voyages, fugitive dust control, volatile organic compound control, and restaurant emission control.

Table 3. Decomposition result of pollution variation between consecutive fall season period (September 1–November 31) of 2009 and 2010 at Guangzhou.

The negative emission-driven effect on PM10 (–25.66 µg m–3) and SO2 (–0.60 ppb) pollution indicates the effectiveness control of emissions measures for fugitive dust and coal combustion-related sources such as power plants and factories. Although the mean concentration of NOx reduced by 0.83 ppb, the decomposition result shows that the emission-driven effect of NO2 increased by 1.98 ppb in 2010. Instead, meteorology-driven effect caused the observed reduction in NOx during the Guangzhou Asian Games. The aggravation of emission-driven NO2 and O3 implies that the implemented strategies were not effective, despite the conventional traffic restrictions also prohibit heavily polluted vehicles (vehicles with yellow signs) going on road. This meteorology-driven exacerbation is in line with the study of Lu et al. (2013), which revealed that, during the Asian Game, the largest contributor of NOx was on-road mobile source while vehicular emission control might be inefficient for NO2 reduction. This analysis shows an example that the absolute pollution reduction does not guarantee with the positive effectiveness of emission control. In summary, wind effects led to reductions (3%–357%) in the concentrations of the primary pollutants in fall 2010 compared to fall 2009, while emission-driven effect has a cleaning impact on SO2 and PM10 but an aggravation on NO2. These results indicate that the control policies during the Guangzhou Asian Games were effective only for SO2 and PM10 pollution (Tao et al., 2015) but not for NO2 pollution which is similar to Shanghai Expo.

3.4 Analysis for 2020 Wuhan Lockdown

The WPD method was also applied to quantify the emission-driven and meteorology-driven effects on air quality during the COVID-19 lockdown period in Wuhan. We selected the period from 23 January to 10 March in 2020, and compared it to the same period in 2019. Hourly air quality data (PM2.5, NO2, SO2, O3 and O3_8h) were obtained from two stations selected based on the prevailing northeast wind direction in Wuhan. O3_8h is the mean ozone concentration in the previous 8 hours. Ganghua station (in Qingshan District) and Moon Lake station (in Hanyang District) were selected (see Fig. S1 in Supporting Information for map). Ganghua Station located in the northeast corner of downtown Wuhan, and Moon Lake Station is located at the center of downtown Wuhan. Table 4 shows the decomposition results comparing the selected period with the corresponding period in 2019. Significant reductions are observed in the mean concentrations of all pollutants except O3 and O3_8h. The non-wind effect, mainly driven by local emissions, made the dominant contribution of 99%–147% to the observed pollution reduction. L index of all pollutants ranged from 0.91 to 0.99, indicating the reliability of the decomposition results. The mean PM2.5 concentration during the selected period in 2019 are 79.43 µg m–3 at Ganghua Station and 70.98 µg m–3 at Moon Lake Station, with a decrease for 28.28 µg m–3 and 38.84 µg m–3 respectively. But the wind effect did not substantially lower the PM2.5 concentration, even aggravated the SO2 and NO2. The contaminating wind effect indicates a regional transport contribution, which is supported by Lian et al. (2020)’s study. Zhang et al. (2020) further indicated this transport is a result of relative high-polluted level of the surrounding provinces, due to more anthropogenic activities (Lian et al., 2020; Zhang et al., 2020). The emission-driven effect was close to 100% or > 100%, indicating the significant emission-driven impact on air quality improvement during the COVID-19 lockdown. A noticeable fact is that, significant reduction of NOx and PM2.5 appeared together with an enhancement of O3, especially in urban region, which could be on the score of weakened NOx-titration effect (Li et al., 2013b; Le et al., 2020), weakened uptakes of HO2 radicals (Li et al., 2019), and increased photolysis rate due to the significant PM2.5 reduction (Gao et al., 2020). Increasing O3 concentration could lead to an enhancement of atmospheric oxidability and production of secondary aerosol especially in the urban area (Le et al., 2020), although it is not exceeding the air quality standard.

Table 4. Decomposition result during Wuhan lockdown (23 January–10 March, 2020) compared to the corresponding period of 2019.

3.5 Implication of Event Comparisons

To compare the different events, the decomposition results of the different events are shown in Table 5. The effectiveness of the emission change during Wuhan Lockdown was the most effective (64% NO2 and 54% PM2.5 reductions due to nearly complete emissions shutdown), followed by the Beijing Olympics (42% PM2.5 and 31% NO2 reductions); the Shanghai Expo and the Guangzhou Asian Games showed 24% and 10% emission-driven reductions in PM pollution, respectively.

Table 5. Comparison of the decomposition results of the four events.

A negligible emission-driven NO2 reduction during the Expo event and an increased emission-driven effect (6%) for NO2 pollution during the Guangzhou Asian Games indicate that the strategies applied for NOx control from on-road vehicles are not as effective as those applied for PM and SO2, further indicating the traffic restriction impact on emission control is not as thorough as construction suspension and industry shutdown. Compared with Wuhan Lockdown that almost no vehicles on road, partial traffic restriction in Asian Game and World Expo is not fully effective to control NOx. The results imply that further NOx reductions will require more effective control measures (e.g., further improve the fuel quality, promote green cars) than just prohibiting some vehicles from being on the road.

Large regional pollution transport can still be found in some events (e.g., Wuhan and Shanghai), which indicate a stronger regional-joint prevention for emission control is highly required to completely improve air quality. Beijing had a better regional control because air quality improvement was observed in nearby cities, Tianjin and Shijiazhuang (Mijling et al., 2009). The two Olympic Game have similar control strategies but differ from effectiveness (E_ratio of PM: Beijing 42% and Guangzhou 24%). The reason is Beijing has stronger regional-joint control strategies and a more strict regulation of factory closure, of which hundreds shutdown or relocation were implemented than that for Guangzhou. The COVID-19 case shows a largest impact of E_ratio among all events, which should be achieved by shutting down majority of the emission sources, not only Wuhan but almost nationwide (Le et al., 2020). However, the impact on air quality improvement are not as effective as expected with such an extreme emission closure. The concentration of PM2.5 in Wuhan Lockdown is very close to the national-II air quality standard (NAQS-II, 35 µg m–3), which may convey the enormous difficulty of attaining the NAQS-II at a normal (non-lockdown) condition.

In addition, emission-driven effects increased ozone levels during the Wuhan Lockdown and the Guangzhou Asian Games. Despite the significant reduction (64%) in NO2 during the Wuhan Lockdown, the mean ozone showed a > 60% increase compared to 2019. Though the average ozone level at non-lockdown period is very low (15.98–26.53 ppb) and no ozone episodes occurred during the winter, the increase in emission-driven ozone levels during Wuhan Lockdown still imply the possible ozone increases in the significant reduction case of NOx and PM2.5. Therefore, simply shutting down all emission sources is apparently not an effective way to inhibit ozone pollution. Further understanding the behavior of the chemical and physical interaction between the ozone and PM/NOx should help us find better solution for advanced control strategies and improving future air quality.

One thing worth to be highlighted is that the WPD method provides an objective and robust tool to quantify meteorology-driven and emission-driven impacts on air quality changes at the inter-annual scale and only using routine air quality data, which is easy to be applicable for any other cites or periods. This analysis show an example of using the WPD to comparing the integrated emission control impact on the air quality among different event, which could provide insight into the future air quality management for any city.  


We note that the decomposed wind-driven effect for primary pollutants may not be exactly equal to the meteorological impact on air quality, which also includes variations in wet deposition due to precipitation changes; chemical reaction rate related to solar radiation intensity; hygroscopic particle growth related to humidity, and etc. However, the derived wind-driven effect is not only reflect the impact of wind change, but also the impact due to the change of other meteorological parameters varying at the same time, since the wind and other parameters frequently vary together. For example, the PM pollution will be dissipated when the temperature and relative humidity decrease and northerly wind strengthened in wintertime in Beijing. Therefore, the wind-driven effect can be applied as an indicator for the dominating meteorological impact when treating such a short period, especially for NO2 and SO2.

To estimate the uncertainties of using wind-driven effect to represent the meteorology-driven effect, we also include several related meteorology parameters (including temperature, relative humidity and precipitation) into this decomposition analysis. By introducing multiple parameters in the wind rose grouping, sample size in each grouping decreased (e.g., if one parameter is missing, all type of data at this specific time is abandoned), and unmatched grouping pairs increased between the study period of two years (e.g., when specific wind speed/direction combinations only occur in one period, but not in the other). All of them may cause a failure of applying the decomposition analysis. To ensure the reliability of the results, analysis is only applied when the deviation of calculated expected value from the arithmetic mean is less than 5%. Due to this issues, some of those failed to derive decomposition results by the improved WPD analysis. Fortunately, some of results are satisfying the criterion and statistically valid.

Table 6 shows the result of WPD analysis and the improved WPD analysis by combing other meteorological parameters in Wuhan Lockdown. As shown, emission effect derived from the two methods are very close, of which difference are smaller than 3%. The change of non-wind term and nonlinear term are around 10% in this case, probably due to better representative of meteorological effect or the uncertainties caused by limited data size, which we do not discuss further in this analysis. Other valid results also show that the non-wind effects are quite stable from the two analysis (not shown). The stable non-wind effect indicate that the derived non-wind effect is a reasonable approximation of the non-meteorology-driven effect (i.e., emission-driven effect) in these events. Concentration variations might attribute to (1) the wind-driven effect also include meteorological effects induced by parameters other than wind, which frequently varies with the wind concurrently (e.g. In Beijing, the northerly generally bring cold and dry airmass; In Guangzhou, the southerly generally bring warm and moisture airmass); (2) the sensitivity of other meteorological parameters is less than wind variations in these short events during such short periods; (3) the dominant role of the emission-driven impact with enforced emission reduction in the four events. However, the representativeness of wind-driven effect for meteorology-driven effect at other cities and long-term analysis should be further examined. The further improvement should be carried out for the method to be applied to evaluate meteorology-driven effect on the year-to-year air quality variation in the future.

Table 6. Decomposition result during Wuhan lockdown (January 23–March 10, 2020) applied on WPD (wind only) and improved WPD with other meteorological parameters.


In this study, to assess effectiveness of the emission control strategies have been carried out in China, we used the WPD method to quantify the effectiveness of the integrated control programmes implemented for the largest three international social events as well as the passive emission reduction during the COVID-19 Lockdown in Wuhan. The emission-driven and meteorology-driven impacts on the observed air quality changes during these events were quantified and compared based on the best available observational data. Based on the quantified results with this objective and robust method, we first compare the control effectiveness of the different mega-events together.

The emission-driven factor generally had the most important role in significant pollution variations (> 86%). The emission-driven pollution reduction was largest in the Wuhan Lockdown (64% NO2 and 54% PM2.5 reductions), followed by Beijing Olympics (42% PM2.5 and 31% NO2 reductions) and smallest in the longest lasting Shanghai Expo event. Shutdown or emission control measures applied to industries and power plants are significantly effective for SO2, NO2 and PM2.5 reduction, but those applied to on-road traffic control are less-effective for reducing NO2, even not works for O3 reduction. The Wuhan COVID-19 (with such an extreme emission reduction) impact on air quality improvement was not as effective as expected especially for O3, which further implies the difficulty of air quality attainment in case of non-lockdownThere were also several specific failures that are worth highlighting. (1) During the Shanghai Expo event, the decomposition results revealed that the emission-driven factors played a positive role in air quality improvement (108%–85% removal) for most stations and pollutants, but except for urban NO2 pollution due to less-effective control for on-road traffic as well as the massive number of visitors’ vehicles. (2) Though the mean value of PM10 decreased significantly from 2009 to 2010, the positive emission-driven contribution from the southeast indicated the failed control of biomass burning during the summer of 2010, despite the prohibition on open biomass burning was a regional-joint control statute (by Shanghai, Jiangsu, and Zhejiang governments) during the Expo period, which suggests that the ongoing supervision of control strategies is a key issue to air quality management in future. (3) A decrease of mean NO2 concentration was observed (0.83 ppb) during the Guangzhou event, but the decomposition results revealed that the reduction in NO2 was due to the wind effect; the emission-driven effect on NO2 actually aggravated pollution by 1.98 ppb in 2010, which indicates the failure for NO2 control in Guangzhou (same as Shanghai). (4) The applied control strategies seem to be less-effective, at least ineffective for ozone. In terms of future air quality management in China, the reduction of on-road exhaust emission and ozone pollution is one of the major challenges. It is necessary to introduce advanced control measures for vehicle exhaust, and implement control strategies considering the chemical and physical coupling between ozone and NOx/VOC/PM.


This research supported by the National Natural Science Foundation of China (Grant No. 41961160728 and 41575106), the Guangdong Basic and Applied Basic Research Fund Committee (2020B1515130003), Shenzhen Science and Technology Program (KQTD20180411143441009), Guangdong Province Science and Technology Planning Project of China (Grant 2017A050506003), Key Special Project for Introduced Talents Team of Southern Marine Science and Engineering Guangdong Laboratory (Guangzhou) (GML2019ZD0210), and Shenzhen Key Laboratory Foundation (ZDSYS20180208184349083). We also thank the Dr. Jacky Fu from Shanghai Environment Monitoring Center and Dr. Tong Zhu for providing the data for the study.


On behalf of all authors, the corresponding author states that there is no conflict of interest.


  1. Bherwani, H. (2020). Valuation of air pollution externalities: Comparative assessment of economic damage and emission reduction under COVID-19 lockdown. Air Qual. Atmos. Health 13, 683–694. https://doi.org/10.1007/s11869-020-00845-3

  2. Chen, Yuan, Schleicher, N., Chen, Yizhen, Chai, F., Wang, S., Norra, S. (2013). The Effect of Government Policies on the Temporal Development of Contamination Characteristics Within the Aerosol Distribution in Beijing, China, in: Rauch, S., Morrison, G., Norra, S., Schleicher, N. (Eds.), Urban Environment, Springer Netherlands, Dordrecht, pp. 313–321. https://doi.org/10.1007/978-94-007-7756-9_27

  3. Cheng, Z., Wang, S., Jiang, J., Fu, Q., Chen, C., Xu, B., Yu, J., Fu, X., Hao, J. (2013). Long-term trend of haze pollution and impact of particulate matter in the Yangtze River Delta, China. Environ. Pollut. 182, 101–110. https://doi.org/10.1016/j.envpol.2013.06.043

  4. Chung, K.K., Chan, J.C.L., Ng, C.N., Lam, K.S., Wang, T. (1999). Synoptic conditions associated with high carbon monoxide episodes at a coastal station in Hong Kong. Atmos. Environ. 33, 3087–3095. https://doi.org/10.1016/S1352-2310(97)00328-2

  5. Fu, Q.Y., Wei, H.P., Huang, Y.M, Gao, S., Duan, Y.S., Zhang, Y.H. (2011). Characteristics on Air Quality during the 2010 Shanghai Expo. The 7th Asian Aerosol Conference, Xi’ an, China.

  6. Gao, J., Li, Y., Zhu, B., Hu, B., Wang, L., Bao, F. (2020). What have we missed when studying the impact of aerosols on surface ozone via changing photolysis rates? Atmos. Chem. Phys. 20, 10831–10844. https://doi.org/10.5194/acp-20-10831-2020

  7. Gao, X., Nie, W., Xue, L., Wang, T., Wang, X., Gao, R., Wang, W., Yuan, C., Gao, J., Ravi, K.P., Wang, J., Zhang, Q. (2013). Highly time-resolved measurements of secondary ions in PM2.5 during the 2008 Beijing Olympics: The impacts of control measures and regional transport. Aerosol Air Qual. Res. 13, 367–376. https://doi.org/10.4209/aaqr.2012.04.0083

  8. Gao, Y., Liu, X., Zhao, C., Zhang, M. (2011). Emission controls versus meteorological conditions in determining aerosol concentrations in Beijing during the 2008 Olympic Games. Atmos. Chem. Phys. 11, 12437–12451. https://doi.org/10.5194/acp-11-12437-2011

  9. Gietl, J.K., Klemm, O. (2009). Analysis of traffic and meteorology on airborne particulate matter in Münster, Northwest Germany. J. Air Waste Manage. Assoc. 59, 809–818. https://doi.org/10.3155/1047-3289.59.7.809

  10. Hao, N., Valks, P., Loyola, D., Cheng, Y.F., Zimmer, W. (2011). Space-based measurements of air quality during the World Expo 2010 in Shanghai. Environ. Res. Lett. 6, 044004. https://doi.org/10.1088/1748-9326/6/4/044004

  11. Huang, K., Zhuang, G., Lin, Y., Wang, Q., Fu, J.S., Fu, Q., Liu, T., Deng, C. (2013). How to improve the air quality over megacities in China: Pollution characterization and source analysis in Shanghai before, during, and after the 2010 World Expo. Atmos. Chem. Phys. 13, 5927–5942. https://doi.org/10.5194/acp-13-5927-2013

  12. Huang, X.F., He, L.Y., Xue, L., Sun, T.L., Zeng, L.W., Gong, Z.H., Hu, M., Zhu, T. (2012). Highly time-resolved chemical characterization of atmospheric fine particles during 2010 Shanghai World Expo. Atmos. Chem. Phys. 12, 4897–4907. https://doi.org/10.5194/acp-12-4897-2012

  13. Katsoulis, B.D. (1988). Some meteorological aspects of air pollution in Athens, Greece. Meteorl. Atmos. Phys. 39, 203–212. https://doi.org/10.1007/BF01030298

  14. Le, T., Wang, Y., Liu, L., Yang, J., Yung, Y.L., Li, G., Seinfeld, J.H. (2020). Unexpected air pollution with marked emission reductions during the COVID-19 outbreak in China. Science 369, 702–706. https://doi.org/10.1126/science.abb7431

  15. Li, K., Jacob, D.J., Liao, H., Shen, L., Zhang, Q., Bates, K.H. (2019). Anthropogenic drivers of 2013–2017 trends in summer surface ozone in China. Proc. Natl. Acad. Sci. USA 116, 422–427. https://doi.org/10.1073/pnas.1812168116

  16. Li, X., He, K., Li, C., Yang, F., Zhao, Q., Ma, Y., Cheng, Y., Ouyang, W., Chen, G. (2013a). PM2.5 mass, chemical composition, and light extinction before and during the 2008 Beijing Olympics: PM2.5 and light extinction in Beijing. J. Geophys. Res. 118, 12158–12167. https://doi.org/10.1002/2013JD020106

  17. Li, Y., Lau, A.K.H., Fung, J.C.H., Zheng, J.Y., Zhong, L.J., Louie, P.K.K. (2012a). Ozone source apportionment (OSAT) to differentiate local regional and super-regional source contributions in the Pearl River Delta region, China. J. Geophys. Res. 117, D15305. https://doi.org/10.1029/2011JD017340

  18. Li, Y., Lau, A., Wong, A., Fung, J. (2014). Decomposition of the wind and non-wind effects on observed year-to-year air quality variation: Wind and pollution decomposition. J. Geophys. Res. 119, 6207–6220. https://doi.org/10.1002/2013JD021300

  19. Li, Y., Lau, A.K.H., Fung, J.C.H., Zheng, J., Liu, S. (2013b). Importance of NOx control for peak ozone reduction in the Pearl River Delta region. J. Geophys. Res. 118, 9428–9443. https://doi.org/10.1002/jgrd.50659

  20. Li, Y.T., Deng, X.J., Fan, S.J., Wu, D., Li, F., Deng, T., Tan, H.B., Jiang, D.H. (2012b). Study on air quality and pollution meteorology conditions of Guangzhou during the 2010 Asian games. Environ. Sci. Technol. 33, 2932–2938. (in Chinese with English Abstract)
  21. Lian, X., Huang, J., Huang, R., Liu, C., Wang, L., Zhang, T. (2020). Impact of city lockdown on the air quality of COVID-19-hit of Wuhan city. Sci. Total Environ. 742, 140556. https://doi.org/10.1016/j.scitotenv.2020.140556

  22. Lin, H., Zhang, Y., Liu, T., Xiao, J., Xu, Y., Xu, X., Qian, Z., Tong, S., Luo, Y., Zeng, W., Ma, W. (2014). Mortality reduction following the air pollution control measures during the 2010 Asian Games. Atmos. Environ. 91, 24–31. https://doi.org/10.1016/j.atmosenv.2014.03.051

  23. Lin, J.T., Pan, D., Zhang, R.X. (2013a). Trend and interannual variability of Chinese air pollution since 2000 in association with socioeconomic development: A brief overview. Atmos. Oceanic Sci. Lett. 6, 84–89. https://doi.org/10.1080/16742834.2013.11447061

  24. Lin, Y., Huang, K., Zhuang, G., Fu, J.S., Xu, C., Shen, J., Chen, S. (2013b). Air quality over the Yangtze River Delta during the 2010 Shanghai Expo. Aerosol Air Qual. Res. 13, 1655–1666. https://doi.org/10.4209/aaqr.2012.11.0312

  25. Liu, H., Wang, X., Zhang, J., He, K., Wu, Y., Xu, J. (2013). Emission controls and changes in air quality in Guangzhou during the Asian Games. Atmos. Environ. 76, 81–93. https://doi.org/10.1016/j.atmosenv.2012.08.004

  26. Liu, Y., Yuan, B., Li, X., Shao, M., Lu, S., Li, Y., Chang, C.C., Wang, Z., Hu, W., Huang, X., He, L., Zeng, L., Hu, M., Zhu, T. (2015a). Impact of pollution controls in Beijing on atmospheric oxygenated volatile organic compounds (OVOCs) during the 2008 Olympic Games: Observation and modeling implications. Atmos. Chem. Phys. 15, 3045–3062. https://doi.org/10.5194/acp-15-3045-2015

  27. Liu, Z., Hu, B., Wang, L., Wu, F., Gao, W., Wang, Y. (2015b). Seasonal and diurnal variation in particulate matter (PM10 and PM2.5) at an urban site of Beijing: Analyses from a 9-year study. Environ. Sci. Pollut. Res. 22, 627–642. https://doi.org/10.1007/s11356-014-3347-0

  28. Lo, J.C.F., Lau, A.K.H., Fung, J.C.H., Chen, F. (2006). Investigation of enhanced cross-city transport and trapping of air pollutants by coastal and urban land-sea breeze circulations. J. Geophys. Res. 111, D14104. https://doi.org/10.1029/2005JD006837

  29. Lu, Q., Zheng, J., Ye, S., Shen, X., Yuan, Z., Yin, S. (2013). Emission trends and source characteristics of SO2, NOx, PM10 and VOCs in the Pearl River Delta region from 2000 to 2009. Atmos. Environ. 76, 11–20. https://doi.org/10.1016/j.atmosenv.2012.10.062

  30. Ministry of Environmental Protection (MEP) (2001). The tenth five-year plan. China. (in Chinese)

  31. Ministry of Environmental Protection (MEP) (2005). Flue gas limestone/limegypsum desulfurization project technical specification of thermal power plant. China. (In Chinese)

  32. Ministry of Environmental Protection (MEP) (2006). The eleventh five-year plan. China. (in Chinese)

  33. Ministry of Environmental Protection (MEP) (2010). Engineering technical specification of flue gas selective non-catalytic reduction enitration for thermal power plant. China. (in Chinese)

  34. Ministry of Environmental Protection (MEP) (2011). The twelfth five-year plan. China. (in Chinese)

  35. Ministry of Environmental Protection (MEP) (2013). Air pollution prevention and control action plan. China. (in Chinese)

  36. Mijling, B., van der A, R.J., Boersma, K.F., Van Roozendael, M., De Smedt, I., Kelder, H.M. (2009). Reductions of NO2 detected from space during the 2008 Beijing Olympic Games. Geophys. Res. Lett. 36, L13801. https://doi.org/10.1029/2009GL038943

  37. Nirel, R., Dayan, U. (2001). On the ratio of sulfur dioxide to nitrogen oxides as an indicator of air pollution sources. J. Appl. Meteorol. 40, 1209–1222. https://www.jstor.org/stable/26184852

  38. Norra, S., Yu, Y., Dietze, V., Schleicher, N., Fricker, M., Kaminski, U., Chen, Y., Stüben, D., Cen, K. (2016). Seasonal dynamics of coarse atmospheric particulate matter between 2.5 µm and 80 µm in Beijing and the impact of 2008 Olympic Games. Atmos. Environ. 124, 109–118. https://doi.org/10.1016/j.atmosenv.2015.08.029

  39. Tao, J., Zhang, L., Zhang, Z., Huang, R., Wu, Y., Zhang, R., Cao, J., Zhang, Y. (2015). Control of PM2.5 in Guangzhou during the 16th Asian Games period: Implication for hazy weather prevention. Sci. Total Environ. 508, 57–66. https://doi.org/10.1016/j.scitotenv.2014.11.074

  40. United Nations Environment Programme (UNEP) (2009). UNEP Environmental assessment: Expo 2010 Shanghai, China. UNEP.

  41. Wang, S., Zhao, M., Xing, J., Wu, Y., Zhou, Y., Lei, Y., He, K., Fu, L., Hao, J. (2010). Quantifying the air pollutants emission reduction during the 2008 Olympic Games in Beijing. Environ. Sci. Technol. 44, 2490–2496. https://doi.org/10.1021/es9028167

  42. Wang, T., Lam, K.S., Lee, A.S.Y., Pang, S.W., Tsui, W.S. (1998). Meteorological and chemical characteristics of the photochemical ozone episodes observed at Cape D’Aguilar in Hong Kong. J. Appl. Meteorol. 37, 1167–1178.

  43. Wang, W., Primbs, T., Tao, S., Simonich, S.L.M. (2009a). Atmospheric particulate matter pollution during the 2008 Beijing Olympics. Environ. Sci. Technol. 43, 6440–6440. https://doi.org/10.1021/es901953s

  44. Wang, X., Westerdahl, D., Chen, L.C., Wu, Y., Hao, J., Pan, X., Guo, X., Zhang, K.M. (2009b). Evaluating the air quality impacts of the 2008 Beijing Olympic Games: On-road emission factors and black carbon profiles. Atmos. Environ. 43, 4535–4543. https://doi.org/10.1016/j.atmosenv.2009.06.054

  45. Wang, X., Wang, T., Pathak, R.K., Hallquist, M., Gao, X., Nie, W., Xue, L., Gao, J., Gao, R., Zhang, Q., Wang, W., Wang, S., Chai, F., Chen, Y. (2013). Size distributions of aerosol sulfates and nitrates in Beijing during the 2008 Olympic Games: Impacts of pollution control measures and regional transport. Adv. Atmos. Sci. 30, 341–353. https://doi.org/10.1007/s00376-012-2053-4

  46. Wang, Y., Hao, J., McElroy, M.B., Munger, J.W., Ma, H., Chen, D., Nielsen, C.P. (2009c). Ozone air quality during the 2008 Beijing Olympics: Effectiveness of emission restrictions. Atmos. Chem. Phys. 9, 5237–5251. https://doi.org/10.5194/acp-9-5237-2009

  47. World Bank (2015). East Asia’s Changing Urban Landscape: Measuring a Decade of Spatial Growth. Washington, DC, USA.

  48. Xing, J., Zhang, Y., Wang, S., Liu, X., Cheng, S., Zhang, Q., Chen, Y., Streets, D.G., Jang, C., Hao, J., Wang, W. (2011). Modeling study on the air quality impacts from emission reductions and atypical meteorological conditions during the 2008 Beijing Olympics. Atmos. Environ. 45, 1786–1798. https://doi.org/10.1016/j.atmosenv.2011.01.025

  49. Xu, H.M., Tao, J., Ho, S.S.H., Ho, K.F., Cao, J.J., Li, N., Chow, J.C., Wang, G.H., Han, Y.M., Zhang, R.J., Watson, J.G., Zhang, J.Q. (2013). Characteristics of fine particulate non-polar organic compounds in Guangzhou during the 16th Asian Games: Effectiveness of air pollution controls. Atmos. Environ. 76, 94–101. https://doi.org/10.1016/j.atmosenv.2012.12.037

  50. Yang, L., Wu, Y., Li, J., Song, S., Zheng, X., Hao, J. (2015). Mass concentrations and temporal profiles of PM10, PM2.5 and PM1 near major urban roads in Beijing. Front. Environ. Sci. Eng. 9, 675–684. https://doi.org/10.1007/s11783-014-0731-4

  51. Yao, Z., Zhang, Y., Shen, X., Wang, X., Wu, Y., He, K. (2013). Impacts of temporary traffic control measures on vehicular emissions during the Asian Games in Guangzhou, China. J. Air Waste Manage. Assoc. 63, 11–19. https://doi.org/10.1080/10962247.2012.724041

  52. Zhang, R., Zhang, Y., Lin, H., Feng, X., Fu, T.M., Wang, Y. (2020). NOx emission reduction and recovery during COVID-19 in East China. Atmosphere 11, 433. https://doi.org/10.3390/atmos11040433

Share this article with your colleagues 


Subscribe to our Newsletter 

Aerosol and Air Quality Research has published over 2,000 peer-reviewed articles. Enter your email address to receive latest updates and research articles to your inbox every second week.

77st percentile
Powered by
   SCImago Journal & Country Rank

2022 Impact Factor: 4.0
5-Year Impact Factor: 3.4

Call for Papers for the special issue on: "Carbonaceous Aerosols in the Atmosphere"

Aerosol and Air Quality Research partners with Publons

CLOCKSS system has permission to ingest, preserve, and serve this Archival Unit
CLOCKSS system has permission to ingest, preserve, and serve this Archival Unit

Aerosol and Air Quality Research (AAQR) is an independently-run non-profit journal that promotes submissions of high-quality research and strives to be one of the leading aerosol and air quality open-access journals in the world. We use cookies on this website to personalize content to improve your user experience and analyze our traffic. By using this site you agree to its use of cookies.