Reduction in vehicular emissions attributable to the Covid-19 lockdown in Shanghai: insights from 5 years of monitoring-based machine learning

. Exposure to elemental carbon (EC) and NO x is a public health issue that has been gaining increasing interest, with high exposure levels generally observed in trafﬁc environments, e.g., roadsides. Shanghai, home to approximately 25 million in the Yangtze River Delta (YRD) region in eastern China, has one of the most intensive trafﬁc activity levels in the world. However, our understanding of the trend in vehicular emissions and, in particular, in response to the strict Covid-19 lockdown is limited partly due to the lack of a long-term observation dataset and application of advanced mathematical models. In this study, NO x and EC were continuously monitored at a sampling site near a highway in western Shanghai for 5 years (2016–2020). The long-term dataset was used to train the machine learning model, rebuilding NO x and EC in a business-as-usual (BAU) scenario for 2020. The reduction in NO x and EC attributable to the lockdown was found to be smaller than it appeared because the ﬁrst week of the lockdown overlapped with the Lunar New Year holiday, whereas, at a later stage of the lockdown, the reduction (50 %–70 %) attributable to the lockdown was more signiﬁcant, consistent with the satellite monitoring of NO 2 showing reduced trafﬁc on a regional scale. In contrast, the impact of the lockdown on vehicular emissions cannot be represented well by simply comparing the concentration before and during the lockdown for conventional campaigns. This study demonstrates the value of continuous air pollutant monitoring at a roadside on a long-term basis. Combined with the advanced mathematical model, air quality changes due to future emission control and/or event-driven scenarios are expected to be better predicted.


Introduction
Shanghai is an economic center of China, acting as a major transport hub.In 2019, the number of civilian vehicles was over 4 million in Shanghai, approximately 13 % higher than that in 2017 (Ministry of Transport, 2020).On average, the daily ridership in Shanghai was over 57 million, with the turnover quantity of motor vehicles of approxi-mately 235 000 000 passenger car unit kilometers (Ministry of Transport, 2020).As a response to the Covid-19 outbreak, strict lockdown measures were initiated in major cities across China in 2020, including the megacity of Shanghai in the Yangtze River Delta (YRD) region (He et al., 2020;Wang et al., 2020;Wu et al., 2021).The lockdown measures started in late January and lasted roughly 1 month, during which normal human activities were constrained substantially (Wang et al., 2020;Lin et al., 2023a).The lockdown measures, such as shutting down cross-city travel and requiring people to stay at home, were strictly implemented to minimize human activities (Liu et al., 2020;Zhao et al., 2020).As a result of these restrictive measures, anthropogenic emissions of air pollutants, in particular, vehicular emissions, have been found to be reduced substantially as evidenced by the evolution of NO 2 , which is routinely measured at the ground air quality monitoring site, as well as from satellite monitoring (Li et al., 2021;Wu et al., 2021).
The impacts of vehicular emissions of NO 2 on public health are significant both through direct harm via inhalation and as a precursor to secondary pollutants such as ozone and particulate matter (PM) (Li et al., 2019;Lu et al., 2019;Lin et al., 2023a).Although NO 2 concentration is regulated by air quality standards, NO x (NO + NO 2 ) is only now being limited through new emission standards for new vehicles (Grange et al., 2017).In addition to NO x emissions, on-road vehicles were also a major source of primary PM emissions, comprising various organic and inorganic species (Hallquist et al., 2009;Fuzzi et al., 2015;Lin et al., 2018;Duan et al., 2020;Lin et al., 2020Lin et al., , 2021)).Elemental carbon (EC) or black carbon is a major component of fine PM (PM 2.5 ) from vehicular emissions (Chang et al., 2018;Lin et al., 2020;Jia et al., 2021;Wang et al., 2022c).EC is emitted as a result of incomplete combustion of gasoline or diesel in the internal combustion engine (Lin et al., 2020;Jia et al., 2021), with significant health and climate implications (Ramanathan and Carmichael, 2008;Cappa et al., 2012;Rappazzo et al., 2015;Lin et al., 2023b).Because of the intensive traffic activities in Shanghai, exposure to EC has become a public health issue that has been gaining increasing interest, with high individual EC exposure levels generally observed in traffic environments, e.g., roadsides (Lin et al., 2020;Zhou et al., 2020;Jia et al., 2021).With the recent implementation of high emission standards (e.g.,China IV and V), gasoline vehicles are generally less polluted, in terms of EC emissions, when compared to diesel vehicles (Lin et al., 2020;Huang et al., 2022).Gasoline-powered vehicles currently comprise over 90 % of the total vehicles in China, with the trend of phasing out of vehicles with old emission standards (i.e., China I-III) (J.Wang et al., 2019;M. Wang et al., 2022a).Nevertheless, on-road vehicular emissions are still one of the major sources of NO x and EC in urban China (Zheng et al., 2018;Jia et al., 2021).Moreover, total vehicular emissions are also impacted by traffic mix and volume, vehicle ages, and vehicle speed, while meteorological variables, e.g., wind speed and wind direction, can impact the measured concentrations of air pollutants, making the quantification of vehicular emissions challenging in the real-world ambient environment.
The strict Covid-19 lockdown measures provided a unique opportunity to study the changes in event-driven vehicular emissions (González-Pardo et al., 2022;Borlaza et al., 2023;Hay et al., 2023;Patel et al., 2023), formulating a scientific basis for designing future air quality mitigation strategies.
However, the degree of reduction in vehicular emissions that can be attributable to the Covid-19 outbreak varied greatly in different studies (up to differences of over 2-fold; Jia et al., 2020;Wang et al., 2020;Wu et al., 2021).For example, by directly comparing the NO x concentrations before and during the Covid-19 lockdown period, Jia et al. (2020) found a 56 %-58 % reduction in NO x during the Covid-19 lockdown period in Shanghai.However, the lockdown period overlapped with the Chinese Spring Festival holiday (Wang et al., 2020), during which human activities including traffic were already largely reduced.Moreover, meteorological conditions (e.g., wind speed and direction) may vary, and, therefore, the direct comparison between two different periods does not necessarily reflect the trend in emissions.To decouple the meteorological effects, a meteorological normalization or de-weathering process was first proposed by Grange and Carslaw (2019) using a tree-based machine learning algorithm.Vu et al. (2019) developed the deweathering process to investigate the seasonal trend of typical air pollutants routinely measured in Beijing, and the deweathered pollutants showed a good agreement with the primary emissions from the emission inventory.Using a similar de-weathering process and taking into account the holiday effects, Dai et al. (2021) showed that the reduction (−15.4 %) in NO 2 attributable to the Covid-19 lockdown was, on average, roughly half of the total reduction (−29.5 %) by comparing the measured and counterfactual NO 2 in a businessas-usual (BAU) scenario during the overlapping period in 31 major Chinese cities.The decline in NO 2 attributable to the lockdowns was also shown to be not as large as expected in an analysis of 11 cities globally after a de-weathering process (Shi et al., 2021).However, most of these tree-based machine learning studies did not quantify the importance of the input variables, making these the machine learning process nonexplainable or like a "black box" (Wang et al., 2022a;Lin et al., 2023a).An explainable machine learning algorithm such as the SHapley Additive exPlanation (SHAP) can quantify the impact of meteorological variables (Lundberg et al., 2020;X. Qin et al., 2022;Wang et al., 2022a).However, few studies have applied the explainable machine learning algorithm to study the trend in vehicular emissions.Moreover, most previous studies focused on the changes in the measured NO 2 concentrations, which were routinely measured at an air quality monitoring site (Wang et al., 2020), while few studies reported vehicular EC emissions based on long-term (years) measurement, therefore, limiting our understanding of vehicular PM 2.5 emissions under such a policy intervention and more importantly our ability to predict future air quality changes with similar emission control strategies.
In this study, hourly EC and NO x were continuously measured for 5 years (2016-2020) at a sampling site near a highway in western Shanghai.A machine learning model, i.e., random forest, was applied to train the model to rebuild the measured EC and NO x using meteorological and temporal variables as the model input (Grange et al., 2018;Grange and Carslaw, 2019;Grange et al., 2021;Wang et al., 2022a;Lin et al., 2023a).The SHAP algorithm (Lundberg et al., 2020) was used to quantify the impact of meteorological variables on the measured EC and NO x .A business-as-usual (BAU) scenario was assumed in 2020 and compared with the measured EC and NO x , quantifying the reduction attributable to the lockdown measures.Implications of future emission control measures on vehicular emissions are discussed.

Field sampling
Measurements of NO x and EC were conducted continuously from 2016 to 2020 (5 years) at a sampling site near a highway at the Dianshan Lake (DSL) supersite (31.09 • N, 120.98 • E; approximately 15 m above ground), with two highways (G318 and G50) located approximately 1 km west of the sampling site.The sampling site is located in Qingpu District in western Shanghai (Fig. S1), 50 km west of downtown Shanghai.It is at the intersection of Jiangsu, Shanghai, and Zhejiang provinces.Wind rose analysis showed that the sampling site could be affected by the two nearby highways during both 2016-2019 (normal years) and 2020 (with Covid-19 lockdown measures implemented) (Fig. S2).
Details of the instrument used to measure EC and NO x were provided previously (Jia et al., 2020).Briefly, EC was measured on an hourly basis using a Sunset carbon analyzer (model RT-4, Sunset Laboratory, USA), while hourly NO and NO 2 were monitored using a Thermo Scientific gas analyzer (model 42i, Thermo Fisher Scientific, Massachusetts, USA).The seasonal variation in EC and NO x is shown in Fig. S3.For 2015-2019, the median of EC varied in the range of 1.0-1.5 µg m −3 with higher concentrations in winter than in summer.The median of NO x varied in the range of 45-55 µg m −3 with higher concentrations in winter than in summer for 2015-2019.The Covid-19 lockdown measures were implemented in 2020, resulting in lower concentrations of NO x /EC but a similar seasonal trend (Fig. S3).Meteorological variables of air temperature (air_temp; • C), wind direction (wd; • ), wind speed (ws; m s −1 ), relative humidity (RH; %), pressure (hPa), and rainfall (mm) were measured using a Vaisala automatic weather station (WXT520, Vaisala Ltd., Finland) with a time resolution of 1 h.Satellite images of NO 2 were obtained from the Sentinel-5P Level-3 near-real-time dataset based on the observation of the TROPOspheric Monitoring Instrument (TROPOMI) for 2019 and 2020 (Lin et al., 2023a).The spatial and temporal distribution of vertical column densities (molec.cm −2 ) of tropospheric NO 2 was used to study the changes in vehicular emissions as a response to strict lockdown measures implemented in 2020.

Machine learning setup and validation
A machine learning algorithm -random forest (Grange et al., 2018;Wang et al., 2022a, b) -was deployed to understand the impact of the Covid-19 lockdown on the exhaust emissions from near highways in 2020 based on a businessas-usual (BAU) scenario.A modeling workflow is shown in Fig. S4.NO x and EC were used as a marker of traffic exhaust emissions because traffic was its main contributor in Shanghai (Jia et al., 2021).In this study, the diurnal patterns of EC and NO x show typical rush hour peaks during both the normal and Covid-19 lockdown periods, consistent with the emission pattern from traffic (Fig. S5).
Meteorological (ws, wd, air_temp, RH, rainfall, and pressure) and time (date_unix, day of the year, weekday, hour of the day, and day of the lunar year) variables were used as model inputs to explain the hourly mean EC and NO x concentrations.The time variable of date_unix is the number of seconds since 1 January 1970.Because the day of the Lunar New Year is different in the Gregorian calendar, it was necessary to include the day of the lunar year to better represent the Chinese Lunar New Year holiday, which usually causes a reduction in pollutant concentration (Wang et al., 2020;Dai et al., 2021).For each random forest, the number of trees in the forest was set to 300, while a minimal nod size was set to 5 following Grange et al. (2018).
The time resolution for the random forest features and the target was 1 h.The Covid-19 lockdown started in late January 2020 and lasted roughly 1 month (see Fig. 1).The number of data points modeled in the random forest model was 6244, covering 1 month before and after the start of the Covid-19 lockdown for the same period for 5 years (Fig. 1).Data with missing values were excluded (8 % of the data).Data before the start of the Lunar New Year (i.e., 24 January 2020) were used to train and test the model with a total number of data points of 5616; 80 % (4493 data points) of the dataset was randomly selected to train the dataset, while the remaining 20 % (1123 data points) of the dataset was used to test the model.The training-testing percentages followed Grange et al. (2021).The random forest model was run using the latest "rmweather" R package (Grange et al., 2018).Based on the built forest, data after the Lunar New Year were estimated using the features during the Covid-19 period, i.e., the BAU scenario (Fig. S4).
Validation of the developed random forest was performed by comparing the time series of the predicted and measured NO x /EC for both the testing and training dataset based on the correlation coefficient R and the root mean square error (RMSE) between the time series of measured and predicted pollutants.The performance of the random forest model was compared to the multilinear regression (MLR) model, in terms of the R value and the RMSE value (Table S1).A good simulation often features a high correlation coefficient https://doi.org/10.5194/acp-23-10313-2023 Atmos.Chem.Phys., 23, 10313-10324, 2023 (>0˙.6)(Grange et al., 2021;González-Pardo et al., 2022;Y. Qin et al., 2022).The time series of the predicted NO x /EC showed a good agreement with the measured ones with correlation coefficients in the range of 0.89-0.98 and slopes close to unity, suggesting the developed random forest model captured the variation in the target pollutant well.Moreover, the RMSE values are smaller for the random forest model (i.e., 0.27-0.51for training-testing and 12.94-29.34µg m −3 for EC and NO x , respectively) than the MLR (0.96 µg m −3 for EC and 47.6 µg m −3 for NO x ; Table S1).

Quantification of the reduction in pollutants attributable to the Covid-19 lockdown
Based on the developed random forest model, the estimated NO x and EC concentrations in a BAU scenario were derived (Fig. S3).The BAU scenario assumed everything was the same in 2020 as in the previous years.Because the random forest captured the variation in the target pollutant better than the multilinear regression model (Table S1), the estimated NO x and EC concentrations reflected the corresponding pollutant in a BAU scenario better.The long-term measurements of NO x /EC covered multiple years, which is necessary to train the model for comparison with short-term sampling.
The BAU analysis was performed using a function within the rmweather R package (Grange et al., 2018).
The estimated NO x /EC concentrations were compared with the measured ones during the holiday (the first week of the lunar year, 167 data points), transition (from day 8 to the Lantern Festival, i.e., day 15, 206 data points), and after the transition (250 data points), when the lockdown measures were most restrictive.The differences between the estimated and measured NO x /EC are regarded as the portion that can be attributable to the Covid-19 lockdown measures (Grange et al., 2021).Specifically, to get the pollutant concentration in a BAU scenario, a machine learning model was trained by the data over the previous 4 years to capture the variability in pollutant concentrations using the same input variables as detailed in Sect.2.3.1.After training, the grown forest was used to predict pollutant concentrations experienced beyond the training period during the Covid-19 lockdown.As a result, the time series of the predicted pollutant beyond the training period is a counterfactual, representing the model estimation of pollutant concentrations during the BAU scenario.The pollutant concentrations in the BAU scenario were subsequently compared with what was observed, with the differences (in %; Fig. S4) representing the magnitude of the reduction attributable to the Covid-19 lockdown.

Feature importance analysis using the SHAP algorithm
In this study, SHAP (https://github.com/slundberg/shap,last access: 1 July 2023) was applied to explain the output of the machine learning model, quantifying the importance of the meteorological variables (Lundberg et al., 2020;Oukawa et al., 2022).SHAP is a game-theoretic approach that connects optimal credit allocation with local explanations using classic Shapley values and their related extensions (Lundberg et al., 2020).SHAP analysis was performed using the Python package of SHAP (version 0.41.0) and scikit-learn (version 1.2.0).SHAP produced an interpretable machine learning model using an additive feature attribution method (Lundberg et al., 2020).SHAP quantified the contribution of the input meteorological variables to a single prediction at a specific time, producing a SHAP value in the same unit as the target pollutant.An overview of which meteorological variables were most important for predicting NO x /EC was obtained based on the SHAP values of every feature for every time point.The SHAP overview plot sorted meteorological variables by the sum of SHAP value magnitudes over the entire sampling period.SHAP values were obtained to show the distribution of the impacts each meteorological variable had on the model output.

Trend of observed NO x during the holiday period and Covid-19 lockdown
Figure 1a shows the time series of NO x for 4 weeks before and after the start of the Lunar New Year with 5 years (2016-2020) of measurements at the sampling site near a highway in western Shanghai (map shown in Fig. S1).To understand the impact of the Covid-19 lockdown measurements on traffic emissions, we focus on the NO x time series in 2020 in comparison to the averaged time series of NO x (grey line) for the previous 4 years (i.e., the mean of 2016-2019).The beginning of the 2020 lockdown, starting on 24 January, overlapped with the start of the Lunar New Year holiday, when human activities had already been reduced to a large extent as most migrant workers left the city for their hometowns.Therefore, the holiday effects need to be taken into account when evaluating the impact of the national lockdown measures on the measured pollutants at the sampling site near a highway.
For 2016-2019, a large reduction in NO x was seen during the 7 d holiday period when compared to the period before the holiday.After the holiday, NO x levels started to bounce back during the transition period (i.e., the period before the Lantern Festival on day of the year (DOY) 15) and finally reached a similar level after the transition period when compared to that before the holiday (Fig. 1a).Specifically, before the holiday, the mean concentration of NO x was 72.8 µg m −3 (± 68.8 µg m −3 ; 1 standard deviation), while, during the holiday, NO x concentration was 22.6 µg m −3 (± 11.0 µg m −3 ).After the holiday, the NO x levels increased from 42.6 µg m −3 (± 29.4 µg m −3 ) during the transition to 60.6 µg m −3 (± 39.3 µg m −3 ) after the transition period.As a result, compared to the average NO x level (72.8 µg m −3 ) before the holiday, NO x was reduced by over 65 % (i.e., 50.2 µg m −3 ) during the holiday for a normal year.
Similar to 2016-2019, the observed NO x in 2020 was also largely reduced (60 %) during the holiday period when compared to before the holiday (Fig. 1b).Specifically, NO x before the holiday was 79.5 µg m −3 (± 61.9 µg m −3 ), while it was 29.0 µg m −3 (± 4.2 µg m −3 ) during the holiday.Because the Covid-19 lockdown started on the same day as the holiday, the reduction in NO x observed at the sampling site attributable to the lockdown measures was smaller than it appeared.In other words, simply comparing the air pollutant concentration during the first 7 d of the lockdown to that before the lockdown would overestimate the impact of Covid-19 on the measured air pollutant when holiday effects were strong.
However, NO x remained at low levels during the transition and after the transition period in 2020, i.e., the last 2 weeks of the lockdown, instead of rapidly rising as observed in 2016-2019 (Fig. 1).The mean concentration during the transition period was 32.6 µg m −3 (± 9.3 µg m −3 ) and was 34.8 µg m −3 (± 19.7 µg m −3 ) for the last 2 weeks of the lockdown in 2020, which was 25 % and 50 % lower, respectively, when compared to the same period in 2016-2019.Because it usually takes some time for the control measure to take effect, focusing on the first 7 d of the lockdown may not represent the true impact of the Covid-19 lockdown on air quality.Instead, as the lockdown measures took effect, a large reduction in NO x can be seen in the late stages of the lockdown when NO x was supposed to be increasing.Therefore, we focused on the comparison of NO x during the last 2 weeks of the lockdown (labeled as "lockdown" in Fig. 1 and afterward if not specified otherwise) to study the impact of lockdown measures on traffic emissions at this sampling site (discussed in Sect.3.4).

Observed EC reduction attributable to the lockdown control policies
The measured EC at the sampling site near a highway showed a diurnal pattern with a clear morning rush hour peak, consistent with that for NO x (Fig. S5), suggesting EC was mainly affected by the nearby traffic.The measured EC also showed a dependence on wind speed and wind direction, with a higher concentration associated with low wind speed from the southwestern direction, i.e., from the highway (Fig. S6).The conclusion of EC being mainly from traffic is consistent with previous source apportionment studies in Shanghai (Chang et al., 2018;Jia et al., 2021).
Figure 2 shows the time series of EC before and during the 2020 lockdown as well as the average time series of EC (grey line) for the previous 4 years (i.e., the mean of 2016-2019).Similar to NO x , the 2016-2019 EC level during the holiday was reduced due to the reduced traffic (Fig. 2).Specifically, the mean EC concentration was 1.08 µg m −3 (± 1.04 µg m −3 ) during the holiday, roughly 40 % lower compared to that (1.74 ± 1.22 µg m −3 ) before the holiday.During the transition period in 2016-2019, EC increased to 1.03 µg m −3 (± 0.72 µg m −3 ).Afterward, EC increased to 1.53 µgm −3 (± 1.04 µg m −3 ), very close to the levels before the holiday.
For the 2020 Lunar New Year holiday or the first week of the Covid-19 lockdown, EC was also reduced to a level (0.88 ± 0.45 µg m −3 ) similar to 2016-2019 (1.08 µg m −3 ; Fig. 2).Similar to NO x , the EC reduction attributable to the lockdown measures was not as large as it appeared for the period overlapping with the holiday.However, EC remained at a low level during (0.92 ± 0.58 µg m −3 ) and after the transition (0.78 ± 0.48 µg m −3 ) period.This is because the monthlong lockdown measures kept traffic at a low level for a prolonged time.This is consistent with the pattern observed for NO x , further confirming that the measured EC and NO x at this sampling site near a highway were mainly from traffic emissions.The mean EC concentration during the transition period or roughly the second week of the lockdown in 2020 was 10 % lower than the same period in 2016-2019, while the mean EC concentration during the last 2 weeks of the lockdown was 50 % lower than the same period in 2016-2019.The low level of EC during and after the transition period was due to the lockdown measures, reducing the traffic volume and, therefore, reducing the corresponding trafficrelated EC emissions.

Rebuilding the measured NO x and EC using a machine learning algorithm
The measured mass concentrations of atmospheric NO x and EC were affected by the meteorological variables including wind speed and wind direction (Fig. S6).This is particularly true for multiple years of measurement when the meteorological variables varied over these years.Therefore, the concentration measured at different years was not directly comparable when meteorological variables in addition to emission strength varied across years.Moreover, the relationship between the measured NO x /EC and meteorological conditions was not linear.This is demonstrated by the relatively low values of correlation coefficient (i.e., Pearson's R of 0.45-0.48and R 2 of 0.20-0.23)between the rebuilt NO x /EC and the meteorological parameters using the multilinear regression model (Table S1).Therefore, the multilinear regression model failed to rebuild the measured NO x /EC satisfactorily.
Figure 3a shows the scatterplot between the time series of the rebuilt and measured NO x for the training and testing dataset.The predicted NO x correlated well with the measured NO x with a correlation coefficient (R) of 0.89-0.98,suggesting over 80 % of the data (R 2 >0.8) can be explained by the machine learning model.This value is higher than that from the multilinear regression model (Table S1).Therefore, the machine learning model demonstrated a better performance than the multilinear regression model in capturing the relationship between NO x and meteorological variables.
Figure 3b shows the scatterplot between the time series of the predicted and measured EC for the training and testing dataset.Similar to NO x , the rebuilt EC correlated well with the measured EC with a correlation coefficient (R) of 0.9-0.98,suggesting over 80 % (R 2 of 0.81-0.96) of the EC can be explained by the machine learning model.However, for both NO x and EC, the slope of the linear fit was in the range of 0.67-0.85,suggesting the predicted values were, on average, 13 %-33 % lower than the measured values.By examining the data, the lower-than-unity slope was mainly caused by the data points with high concentrations.These data points can be regarded as outliers that were not captured properly by the machine learning model since these data points deviated largely from the averaged values.
To evaluate the importance of different meteorological variables, the SHAP model was applied (see Method). Figure 4a and b show the distribution of SHAP values (in µg m −3 ) obtained during the rebuilding of NO x and EC, respectively, while Fig. 4c and d show the respective mean absolute of the SHAP values.The meteorological variable with a high SHAP value was associated with high importance, whereas a SHAP value closer to 0 means the meteorological variable was less important.For NO x , ws is the most important meteorological variable (Fig. 4), with low ws contributing up to over 100 µg m −3 and high ws contributing negatively to NO x (down to −40 µg m −3 ).Air temperature, RH, wd, and pressure had SHAP values in the range of −40 to 70 µg m −3 , while rainfall was least important with SHAP values of < 10 µg m −3 (Fig. 4a and c).Similarly, ws was also the important variable for EC, with low ws contributing positively to the EC (SHAP value of up to over 2 µg m −3 , Fig. 4b).Wd, pressure, air temperature, and RH had similar SHAP values (< 1.5 µg m −3 ).Although rainfall was less important, high rainfall was associated with low SHAP values (Fig. 4b and d), consistent with the wet deposition of aerosol.

Trend of meteorologically normalized NO x and EC: a business-as-usual scenario
To evaluate the impact of the lockdown in 2020 on NO x /EC emissions at this sampling site near a highway, a businessas-usual (BAU) scenario was assumed.The BAU scenario in 2020 assumed that everything was similar to what would happen previously, i.e., without the lockdown measures.For the BAU scenario in 2020, NO x and EC would drop during the holiday but increase their concentration levels during the transition and reach a level similar to that before the holiday (Fig. 5), as in 2016-2019 (Figs. 1 and 2).Through the comparison of the 2020 BAU to the measured NO x /EC in 2020, the reduction in NO x /EC attributable to Covid-19 can be quantitatively evaluated.NO x and EC concentrations during the holiday, transition, and lockdown periods were normalized to that before the holiday (Fig. 5).For BAU in 2020, NO x during the holiday was reduced to 53 % of the level before the holiday.In comparison, the measured NO x during the holiday was 36 % of the level before the holiday.Therefore, the difference (17 %) between BAU 2020 and 2020 was attributable to the Covid-19 control measures.In other words, the mea- sured NO x was roughly 30 % lower than it would be without the control measures.During the transition period, the NO x level for BAU 2020 returned to ∼ 75 % of the level before the holiday.In comparison, the measured NO x was only 40 % of that before the holiday.Therefore, the measured NO x was approximately 45 % lower than BAU 2020.After the transition period, NO x returned to a level similar to that before the holiday for BAU 2020.However, the measured NO x was only 40 % of that before the holiday.As a result, the NO x reduction attributable to the Covid-19 lockdown measures was the most significant after the transition period, which was approximately 60 % of BAU 2020.Therefore, the month-long lockdown measures kept NO x at a low level consistently, demonstrating the effectiveness of the lockdown in reducing traffic emissions as the lockdown measures continued.
Similar to NO x , EC also showed the largest reduction during the lockdown when compared to BAU 2020 (Fig. 5b).Specifically, EC was roughly 60 % lower during the lockdown in 2020 than the BAU scenario in 2020, while the reduction in EC was 40 % and 30 % lower during the transition and holiday periods, respectively.As a result, both NO x and EC showed a similar level of reduction which was attributable to the lockdown measures.

Reduction in traffic emissions during the Covid-19
lockdown on a regional scale Figure 6 shows the TROPOMI images of NO 2 in the YRD region over the same period, i.e., before the holiday and after the transition, for the years 2019 and 2020.By comparing the vertical column densities of NO 2 monitored over the same period in 2019 and 2020, the evolution of satellite monitoring of NO 2 showed a trend consistent with that observed from the ground monitoring at the sampling site near a highway (Figs.1-3).In particular, a great reduction (50 %-70 %) in NO 2 during the lockdown period in 2020 was seen when compared to that over the same period in 2019, whereas after the transition period in 2020, NO 2 was expected to return to a level similar to that before the holiday, i.e., the BAU scenario  Specifically, the vertical column concentration of NO 2 at DSL was highly elevated before the holiday in 2019, with mean vertical column concentrations of over 18 × 10 15 molec.cm −2 .After the transition period in 2019, NO 2 returned to a slightly lower value (16-18 × 10 15 molec.cm −2 ) compared to that before the holiday.This is consistent with the BAU scenario assumed in 2020 (Fig. 5).In 2020, NO 2 before the holiday was similar to the level over the same period in 2019 (18-20 × 10 15 ).However, during the lockdown period, NO 2 was 8-10 × 10 15 , 50 %-70 % lower than in the same period in 2019.Such a reduction was attributable to the lockdown measures.In addition, the satellite images also demonstrate that traffic emissions were largely reduced during the lockdown on a regional scale in the YRD region.

Discussion
Through the comparison of EC and NO x before and during the lockdown in 2020, as well as the same period in previous years (2016-2019), we showed that determining the reduction in vehicular emissions that could be attributed to the lockdown measures was complicated and cannot be achieved by simply comparing the concentration difference between before and during the lockdown.This is because vehicular emissions have their own trend during the Lunar New Year, when vehicular emissions were largely reduced (Dai et al., 2021).Here, we showed that, due to the overlapping of the first week of the lockdown with the holiday, the reduction in vehicular emissions attributable to the lockdown was smaller than it appeared.This trend can be only revealed from multiple years of continuous measurement and would be easily missed by a conventional field campaign that only lasted a matter of months.For example, Jia et al. (2020) reported a 56 %-58 % reduction in NO x during the Covid-19 lockdown period by directly comparing the NO x concentrations to the period before the holiday in Shanghai.Here, we showed NO x was already reduced by approximately 60 % during the holiday week in a normal year.Such a trend in traffic emissions during the holiday week is consistent with the findings of previous studies (He et al., 2020;Dai et al., 2021;Shi et al., 2021).Considering the holiday effect, Dai et al. (2021) reported a reduction of ∼ 15 % in NO 2 attributable to the Covid-19 lockdown period in Shanghai during the holiday week.This value is similar to this study's 17 % reduction in NO x .However, previous studies focusing only on the holiday week may underestimate the impact of the Covid-19 lockdown on air quality over an extended period because the lockdown period lasted more than 1 week.During the last 2 weeks of the lockdown, a 50 %-70 % reduction in both NO x and EC was attributable to the Covid-19 lockdown.Since the lockdown measures often took time to be executed more extensively, the later stages of air pollution reduction may better represent the air quality effect of Covid-19.
Many studies have shown the impact of the lockdown on traffic emissions but with different degrees of reduction that are attributable to the lockdown (Jia et al., 2020;Wang et al., 2020;Shi et al., 2021).Most previous studies focused on gas pollutants, i.e., NO 2 probably because NO 2 was a regular gas pollutant that is routinely measured at the air quality monitoring sites across the major Chinese cities (He et al., 2020), while few reported the particulate EC emissions from traffic partly due to the scarcity of the dataset.EC is light absorbing and is regarded as a warming agent second only to CO 2 (Jacobson, 2001;Cappa et al., 2012;Liu et al., 2015).In addition, EC is one of the major particulate pollutants that can cause adverse health effects (Rappazzo et al., 2015).To the best of our knowledge, this is the first study to illustrate the impact of the lockdown on vehicular EC emissions at a sampling site near a highway based on 5 years of continuous measurement.Such a dataset is rare in the literature since lockdown measures restrict the movement of instrument operators.Only with good maintenance of the instrument at the sampling site could we keep the sampling going on during the strict lockdown.
To decouple the effects of the meteorological variables on the measured NO x and EC, a machine learning model was trained and tested based on the 5-year dataset.The machine learning model emerges as a powerful model in air quality studies, especially the development of SHAP (Lundberg et al., 2020), making the machine learning model explainable rather than a black box as in most previous air quality studies (Grange et al., 2017;Grange and Carslaw, 2019;Vu et al., 2019;Shi et al., 2021).The explainable machine learning model of SHAP showed that meteorological variables, especially ws and wd, were key parameters that affect the measured levels with concentrations of up to 100 µg m −3 for NO x .Low wind speed indicated poor dispersion conditions that favored the buildup of air pollutants, while wind direction pointed to the emission source of nearby traffic.Due to the important the role of meteorological variables, their impact needs to be removed when evaluating the true impact of the lockdown on vehicular emissions.Here, instead of simply comparing the concentration before and during the lockdown, a BAU scenario was assumed in 2020.This relies on the rebuilding power of the mathematical model.However, to train the machine learning model, a large body of datasets is required as the model input.As more datasets are to be collected and used as model input, the performance of machine learning is expected to improve further.Moreover, with more variables, e.g., vehicular types, weight, and road conditions, being monitored and used as input for the model, better prediction power of the machine learning is anticipated.Correspondingly, the air quality improvement in future emission control scenarios can be better predicted.

Conclusions
In this study, we studied the impact of the Covid-19 lockdown on traffic emissions based on a 5-year measurement of NO x and EC using a BAU scenario analysis at a sampling site near a highway in Shanghai.We showed that (1) by simply comparing the concentration before and during the lockdown, the effects of the lockdown on air pollutant emissions may be overestimated and (2) a large reduction (50 %-70 %) in vehicular emissions of NO x and EC was attributed to the lockdown at a later stage that may better represent the impact of lockdown measures on air quality.This value is larger than previous studies because both the holiday effects and meteorological impacts were removed during this period.This large reduction in vehicular emissions at a later stage was consistent with satellite monitoring of NO 2 .Therefore, the strict lockdown reduced both vehicular gaseous and particulate emissions significantly when holiday and meteorological effects were not affecting the trend analysis.This study demonstrates the importance of continuous monitoring at this Shanghai supersite.When coupled with an advanced mathematical algorithm, insights into the impact of human activities on air pollution can be gained based on long-term monitoring.Air quality improvement in future emission control scenarios is expected to be better predicted.
Data availability.The data presented in this study are available in the Zenodo data archive https://doi.org/10.5281/zenodo.6473085(Wang et al., 2022d).
Author contributions.MW, ZZ, XL, and SH designed the study.YD, JH, JC, YL, and QF conducted field campaigns.MW, YD, ZZ, and QY conducted data analysis.MW prepared the manuscript with contributions from all co-authors.QF, TW, JC, and SL provided input for revision before submission.QF and SL provided project guidance.
Competing interests.The contact author has declared that none of the authors has any competing interests.
Disclaimer.Publisher's note: Copernicus Publications remains neutral with regard to jurisdictional claims in published maps and institutional affiliations.

Figure 1 .
Figure 1.(a) Time series (day of the year; DOY) of the measured NO x for 4 weeks before and after the start of the Lunar New Year for the mean of 2016-2019 and 2020 and (b) mean NO x concentrations for different periods, i.e., before the holiday, holiday, transition, and lockdown.The time series in (a) is a 7 d rolling average.The error bar in (b) stands for 1 standard deviation.Note that the lunar DOY for 2016-2019 was on different Gregorian dates, but these dates were grouped together based on the lunar DOY in (a).

Figure 2 .
Figure 2. (a) Time series (day of the year; DOY) of the measured EC for 4 weeks before and after the start of the Lunar New Year for the mean of 2016-2019 and 2020 and (b) mean EC concentrations for different periods, i.e., before the holiday, holiday, transition, and lockdown.The time series in (a) is a 7 d rolling average.The error bar in (b) stands for 1 standard deviation.

Figure 3 .
Figure 3. Scatterplot between the predicted and measured (a) NO x and (b) EC for the testing and training dataset.Also shown is the linear regression between the predicted and measured values, with the correlation coefficient (R) and p value in the top left.

Figure 4 .
Figure 4. Distribution of SHAP values (in µg m −3 ) for the meteorological variables, i.e., features when building the random forest model, for (a) NO x and (b) EC and mean absolute SHAP values for (c) NO x and (d) EC.

Figure 5 .
Figure 5.Comparison of (a) NO x and (b) EC evolution between the business-as-usual (BAU) scenario and the measured one in 2020.All concentrations were normalized to the level before the holiday.

Figure 6 .
Figure 6.The spatial distribution of TROPOMI NO 2 over the same period in 2019 and 2020 near the DSL sampling site in western Shanghai in the YRD region.

Acknowledgements.
This work was supported by the Startup Fund for RAPs under the Strategic Hiring Scheme (grant no.P0043854); Green Tech Fund (grant no.GTF202110151); Environment and Conservation Fund -Environmental Research, Technology Demonstration and Conference Projects (grant no.ECF 63/2019); RGC Theme-based Research Scheme (grant nos.T24-504/17-N and T31-603/21-N); Key Research and Development Projects of Shanghai Science and Technology Commission (grant no.20dz1204000); and State Ecology and Environment Scientific Observation and Research Station for the Yangtze River Delta at Dianshan Lake (SEED).