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Keywords = WRF-CMAQ

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12 pages, 3102 KiB  
Article
Modeling Analysis of Nocturnal Nitrate Formation Pathways during Co-Occurrence of Ozone and PM2.5 Pollution in North China Plain
by Wei Dai, Keqiang Cheng, Xiangpeng Huang and Mingjie Xie
Atmosphere 2024, 15(10), 1220; https://doi.org/10.3390/atmos15101220 - 13 Oct 2024
Viewed by 456
Abstract
The rapid formation of secondary nitrate (NO3) contributes significantly to the nocturnal increase of PM2.5 and has been shown to be a critical factor for aerosol pollution in the North China Plain (NCP) region in summer. To explore the [...] Read more.
The rapid formation of secondary nitrate (NO3) contributes significantly to the nocturnal increase of PM2.5 and has been shown to be a critical factor for aerosol pollution in the North China Plain (NCP) region in summer. To explore the nocturnal NO3 formation pathways and the influence of ozone (O3) on NO3 production, the WRF-CMAQ model was utilized to simulate O3 and PM2.5 co-pollution events in the NCP region. The simulation results demonstrated that heterogeneous hydrolysis of dinitrogen pentoxide (N2O5) accounts for 60% to 67% of NO3 production at night (22:00 to 05:00) and is the main source of nocturnal NO3. O3 enhances the formation of NO3 radicals, thereby further promoting nocturnal N2O5 production. In the evening (20:00 to 21:00), O3 sustains the formation of hydroxyl (OH) radicals, resulting in the reaction between OH radicals and nitrogen dioxide (NO2), which accounts for 48% to 64% of NO3 formation. Our results suggest that effective control of O3 pollution in NCP can also reduce NO3 formation at night. Full article
(This article belongs to the Section Air Quality)
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Figure 1

Figure 1
<p>The WRF-CMAQ simulation domains, with red and blue dots, denote the locations of meteorological and environmental observation sites. The blue dashed rectangle marked North China Plain.</p>
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<p>Time series of 3 hourly observations (black dashed line) and hourly simulation (red solid line), 2 m temperature (T<sub>2</sub>), 2 m relative humidity (RH<sub>2</sub>), and 10 m wind speed (WS<sub>10</sub>) during the five air pollution episodes. The statistical metric correlation coefficient (<span class="html-italic">R</span>) and normalized mean bias (NMB) are shown.</p>
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<p>Time series of hourly observation (black dashed line) and simulation (red solid line) O<sub>3</sub> (ppb) and PM<sub>2.5</sub> (μg m<sup>−3</sup>) concentration during the five air pollution episodes. The statistical metric correlation coefficient (<span class="html-italic">R</span>) and normalized mean bias (NMB) are shown. The values of 100 μg m<sup>−3</sup> (51 ppb) and 35 μg m<sup>−3</sup> were marked with blue dashed lines, respectively.</p>
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<p>Average diurnal variations in concentrations of major PM<sub>2.5</sub> composition, O<sub>3</sub>, and PM<sub>2.5</sub> during pollution episodes. The black carbon (BC), dust, and primary organic aerosol (POA) are represented as primary aerosol components (PRI).</p>
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<p>Average diurnal variations of (<b>a</b>) HNO<sub>3</sub> and (<b>b</b>) N<sub>2</sub>O<sub>5</sub> production rates by different pathways, and associated with total HNO<sub>3</sub> production rates (HNO3prod), total N<sub>2</sub>O<sub>5</sub> production rates (N2O5prod), HNO<sub>3</sub>, N<sub>2</sub>O<sub>5</sub>, and NO<sub>3</sub> radical concentrations during pollution episodes. “OH + NO<sub>2</sub>”, “HET N<sub>2</sub>O<sub>5</sub>”, “NO<sub>3</sub> + VOC”, “Others” and “NO<sub>2</sub> + NO<sub>3</sub>” represented different chemical reaction pathways described in <a href="#atmosphere-15-01220-t001" class="html-table">Table 1</a> and <a href="#sec2dot1-atmosphere-15-01220" class="html-sec">Section 2.1</a>.</p>
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<p>Average diurnal variations of NO<sub>3</sub> radical production rates from the “O<sub>3</sub> + NO<sub>2</sub>” pathway, the concentration of NO<sub>3</sub> radicals (blue solid line), HO<span class="html-italic"><sub>x</sub></span> radicals (blue dashed line), O<sub>3</sub> (red solid line) and NO<sub>2</sub> (red dashed line). “O<sub>3</sub> + NO<sub>2</sub>” represented chemical reaction pathway is described in <a href="#atmosphere-15-01220-t001" class="html-table">Table 1</a> and <a href="#sec2dot1-atmosphere-15-01220" class="html-sec">Section 2.1</a>.</p>
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19 pages, 10490 KiB  
Article
Source Attribution Analysis of an Ozone Concentration Increase Event in the Main Urban Area of Xi’an Using the WRF-CMAQ Model
by Ju Wang, Yuxuan Cai, Sainan Zou, Xiaowei Zhou and Chunsheng Fang
Atmosphere 2024, 15(10), 1208; https://doi.org/10.3390/atmos15101208 - 10 Oct 2024
Viewed by 369
Abstract
The significant increase in ambient ozone (O3) levels across China highlights the urgent need to investigate the sources and mechanisms driving regional O3 events, particularly in densely populated urban areas. This study focuses on Xi’an, located in northwestern China on [...] Read more.
The significant increase in ambient ozone (O3) levels across China highlights the urgent need to investigate the sources and mechanisms driving regional O3 events, particularly in densely populated urban areas. This study focuses on Xi’an, located in northwestern China on the Guanzhong Plain near the Qinling Mountains, where the unique topography contributes to pollutant accumulation. Urbanization and industrial activities have significantly increased pollutant emissions. Utilizing the Weather Research and Forecasting–Community Multiscale Air Quality Model (WRF-CMAQ), we analyzed the contributions of specific regional and industrial sources to rising O3 levels, particularly during an atypical winter event characterized by unusually high concentrations. Our findings indicated that boundary conditions were the primary contributor to elevated O3 levels during this event. Notably, Xianyang and Baoji accounted for 30% and 22% of the increased O3 levels in Xi’an, respectively. Additionally, residential sources and transportation accounted for 31% and 28% of the O3 increase. Within the Xi’an metropolitan area, Baqiao District (18–27%) and Weiyang District (23–30%) emerged as leading contributors. The primary industries contributing to this rise included residential sources (28–37%) and transportation (35–43%). These insights underscore the need for targeted regulatory measures to mitigate O3 pollution in urban settings. Full article
(This article belongs to the Section Air Quality)
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Figure 1
<p>Map showing the triple-nested simulation domains, urban areas, and topography for each nest.</p>
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<p>Daily mean O<sub>3</sub> concentrations in February 2020 (red line) vs. February 2019 (black line), February 2021 (blue line), February 2022 (green line), and average O<sub>3</sub> concentrations for each month (dashed line).</p>
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<p>Comparison of temperature time series of meteorological stations in Xi’an.</p>
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<p>Comparison of wind-speed time series of meteorological stations in Xi’an.</p>
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<p>Comparison of O<sub>3</sub>-concentration time series in Xi’an.</p>
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<p>Contribution rates of O<sub>3</sub> to the 12 tagged regions under the regional source apportionment scenario. (<b>a</b>,<b>b</b>) are the contribution of each tagged region in d02 to O<sub>3</sub> in 2020 vs. in 2019, (<b>c</b>,<b>d</b>) are the contribution of each tagged region in d03 to O<sub>3</sub> in 2020 vs. in 2019.</p>
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<p>Contribution rates of O<sub>3</sub> to the 12 tagged regions under the source apportionment scenario for different emission types. (<b>a</b>,<b>b</b>) are the contribution of each tagged region in d02 to O<sub>3</sub> in 2020 vs. in 2019, (<b>c</b>,<b>d</b>) are the contribution of each tagged region in d03 to O<sub>3</sub> in 2020 vs. in 2019.</p>
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<p>Contribution rates of O<sub>3</sub> to the tagged regions of d02 under the regional source apportionment scenario in 2019 (<b>a</b>) and 2020 (<b>b</b>).</p>
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<p>Contribution rates of O<sub>3</sub> to the tagged regions of d02 under the source apportionment scenario for different emission types in February 2020: (<b>a</b>) IH; (<b>b</b>) PH; (<b>c</b>) TH; (<b>d</b>) RH.</p>
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<p>Contribution rates of O<sub>3</sub> to the tagged regions of d02 under the source apportionment scenario for different emission types in February 2019: (<b>a</b>) IH; (<b>b</b>) PH; (<b>c</b>) TH; (<b>d</b>) RH.</p>
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<p>Contribution rates of O<sub>3</sub> to the tagged regions of d02 under the source apportionment scenario for different emission types in February 2019: (<b>a</b>) IH; (<b>b</b>) PH; (<b>c</b>) TH; (<b>d</b>) RH.</p>
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<p>Contribution rates of O<sub>3</sub> to the tagged regions of d03 under the regional source apportionment scenario in 2019 (<b>a</b>) and 2020 (<b>b</b>).</p>
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<p>Contribution rates of O<sub>3</sub> to the tagged regions of d03 under the source apportionment scenario for different emission types in February 2020: (<b>a</b>) IH; (<b>b</b>) PH; (<b>c</b>) TH; (<b>d</b>) RH.</p>
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<p>Contribution rates of O<sub>3</sub> to the tagged regions of d03 under the source apportionment scenario for different emission types in February 2019: (<b>a</b>) IH; (<b>b</b>) PH; (<b>c</b>) TH; (<b>d</b>) RH.</p>
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13 pages, 17472 KiB  
Article
High-Resolution Daily PM2.5 Exposure Concentrations in South Korea Using CMAQ Data Assimilation with Surface Measurements and MAIAC AOD (2015–2021)
by Jin-Goo Kang, Ju-Yong Lee, Jeong-Beom Lee, Jun-Hyun Lim, Hui-Young Yun and Dae-Ryun Choi
Atmosphere 2024, 15(10), 1152; https://doi.org/10.3390/atmos15101152 - 26 Sep 2024
Viewed by 438
Abstract
Particulate matter (PM) in the atmosphere poses significant risks to both human health and the environment. Specifically, PM2.5, particulate matter with a diameter less than 2.5 micrometers, has been linked to increased rates of cardiovascular and respiratory diseases. In South Korea, concerns about [...] Read more.
Particulate matter (PM) in the atmosphere poses significant risks to both human health and the environment. Specifically, PM2.5, particulate matter with a diameter less than 2.5 micrometers, has been linked to increased rates of cardiovascular and respiratory diseases. In South Korea, concerns about PM2.5 exposure have grown due to its potential for causing premature death. This study aims to estimate high-resolution exposure concentrations of PM2.5 across South Korea from 2015 to 2021. We integrated data from the Community Multiscale Air Quality (CMAQ) model with surface air quality measurements, the Weather Research Forecast (WRF) model, the Normalized Difference Vegetation Index (NDVI), and the Multi-Angle Implementation of Atmospheric Correction (MAIAC) Aerosol Optical Depth (AOD) satellite data. These data, combined with multiple regression analyses, allowed for the correction of PM2.5 estimates, particularly in suburban areas where ground measurements are sparse. The simulated PM2.5 concentration showed strong correlations with observed values R (ranging from 0.88 to 0.94). Spatial distributions of annual PM2.5 showed a significant decrease in PM2.5 concentrations from 2015 to 2021, with some fluctuation due to the COVID-19 pandemic, such as in 2020. The study produced highly accurate daily average high-resolution PM2.5 exposure concentrations. Full article
(This article belongs to the Special Issue Novel Insights into Air Pollution over East Asia)
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<p>Locations of ambient air quality monitoring stations in the region of China and Korea (blue dots: china monitoring stations, green dots: south korea monitoring stations).</p>
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<p>Modeling domain (Domain 1: East Asia, Domain 2: South Korea).</p>
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<p>Scatter plots of MLRs with observations for 2015–2021.</p>
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<p>Reanalyzed average seasonal PM2.5 distribution in 2015–2021.</p>
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<p>Reanalyzed average seasonal PM2.5 distribution in 2015–2021.</p>
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<p>Reanalyzed annual PM2.5 distribution in 2015–2021.</p>
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17 pages, 5572 KiB  
Article
An Ozone Episode in the Urban Agglomerations along the Yangtze River in Jiangsu Province: Pollution Characteristics and Source Apportionment
by Zhe Cai, Derong Zhou, Jianqiao Yu, Sheng Zhong, Longfei Zheng, Zijun Luo, Zhiwei Tang and Fei Jiang
Atmosphere 2024, 15(8), 942; https://doi.org/10.3390/atmos15080942 - 6 Aug 2024
Viewed by 598
Abstract
A severe ozone episode occurred in cities along the Yangtze River of Jiangsu Province (UAYRJS) from 6 to 8 September 2022, with daily maximum 8-h average ozone concentrations in the range of 65.8–119 ppb, peaking in Nanjing on 7 September. We used the [...] Read more.
A severe ozone episode occurred in cities along the Yangtze River of Jiangsu Province (UAYRJS) from 6 to 8 September 2022, with daily maximum 8-h average ozone concentrations in the range of 65.8–119 ppb, peaking in Nanjing on 7 September. We used the air quality model WRF-CMAQ-ISAM and the Lagrange trajectory model HYSPLIT to quantify the ozone contribution of each region and analyze the causes and regional transmission pathways of ozone pollution in the UAYRJS. Based on simulated emissions, we also estimated the contribution of biogenic volatile organic compounds. We found that weather has a negative impact on pollution, and ozone pollution tracks the movement of the Western Pacific Subtropical High. UAYRJS was affected by oceanic pollution, and there was a mutual influence among the area’s cities. On 6 September, the ozone in UAYRJS was mostly locally generated (50–98%); on 7 September, it was dominated by extra-regional transport (50–80%). Isoprene concentrations in UAYRJS increased by 0.03–0.1 ppb on 6 and 7 September compared with 5 September. Sensitivity testing showed that the hourly ozone concentration increased by 0.1–27.8 ppb (7.6–19.1%) under the influence of biogenic emissions. The results provide a scientific basis for future ozone control measures. Full article
(This article belongs to the Special Issue New Insights in Air Quality Assessment: Forecasting and Monitoring)
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<p>Domain 02’s setting of WRF-CMAQ-ISAM model.</p>
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<p>Evaluation of the simulations of each variable hourly value in UAYRJS from 5 to 8 September 2022.</p>
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<p>O<sub>3–8 h</sub> pollution calendar map in UAYRJS from 5 to 8 September 2022 (unit: ppb). (Note: Green, yellow, orange and red represent excellent, good, light and moderate pollution under the ozone air quality sub-index standards, respectively).</p>
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<p>Height distribution of 588 dgpm potential at an altitude of 500 hPa on 16:00, 5 to 8 September 2022.</p>
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<p>Spatial distribution of ozone concentration changes in UAYRJS from 5 to 8 September 2022. (Note: The shades represent the concentration distribution, and the vector arrows represent the wind direction and speed).</p>
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<p>96 h backward trajectories of UAYRJS at 16:00 on 6 September 2022. (Note: The dots represent the simulated release position; the lines represent the spatial distribution of traceable trajectories).</p>
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<p>Hourly series of ozone source analysis in UAYRJS from 5 to 8 September 2022. (Note: The superimposed slash mask area represents the nighttime, with no mask for daytime. The coloring map depicts the relative contribution from different regions represented by different colors to the hourly concentration in a given city; they add up to a total of 100%. The highly saturated colors represent the UAYRJS, and relatively low saturation represents other areas).</p>
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<p>Hourly observed concentration of isoprene in UAYRJS. (Data for ZJ are missing, so only seven cities’ concentration series are displayed).</p>
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<p>Spatial distribution of daily contribution concentrations (<b>a</b>) and hourly contribution concentration by city (<b>b</b>) to ozone from simulated sources in UAYRJS from 5 to 8 September 2022.</p>
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12 pages, 3421 KiB  
Article
Temporal Refinement of Major Primary Air Pollutant Emissions Based on Electric Power Big Data: A Case of the Cement Industry in Tangshan City
by Xiaoxuan Bai, Peng Li, Weiqing Zhou, Huacheng Wu, Chao Li and Zilong Zhou
Atmosphere 2024, 15(8), 895; https://doi.org/10.3390/atmos15080895 - 26 Jul 2024
Viewed by 466
Abstract
High-temporal resolution and timely emission estimates are essential for developing refined air quality management policies. Considering the advantages of extensive coverage, high reliability, and near real-time capabilities, in this work, electric power big data (EPBD) was first employed to obtain accurate hourly resolved [...] Read more.
High-temporal resolution and timely emission estimates are essential for developing refined air quality management policies. Considering the advantages of extensive coverage, high reliability, and near real-time capabilities, in this work, electric power big data (EPBD) was first employed to obtain accurate hourly resolved facility-level air pollutant emissions information from the cement industries in Tangshan City, China. Then, the simulation optimization was elucidated by coupling the data with the weather research and forecasting (WRF)-community multiscale air quality (CMAQ) model. Simulation results based on estimated emissions effectively captured the hourly variation, with the NMB within ±50% for NO2 and PM2.5 and R greater than 0.6 for SO2. Hourly PM2.5 emissions from clinker production enterprises exhibited a relatively smooth pattern, whereas those from separate cement grinding stations displayed a distinct diurnal variation. Despite the remaining underestimation and/or overestimation of the simulation concentration, the emission inventory based on EPBD demonstrates an enhancement in simulation results, with RMSE, NMB, and NME decreasing by 9.6%, 15.8%, and 11.2%, respectively. Thus, the exploitation of the vast application potential of EPBD in the field of environmental protection could help to support the precise prevention and control of air pollution, with the possibility of the early achievement of carbon peaking and carbon neutrality targets in China and other developing countries. Full article
(This article belongs to the Section Air Pollution Control)
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Figure 1
<p>Comparison of monthly cement production (green column), obtained from the Tangshan Monthly Statistical Report (<a href="https://www.tangshan.gov.cn/zhuzhan/sjfb/index.html" target="_blank">https://www.tangshan.gov.cn/zhuzhan/sjfb/index.html</a>, accessed on 25 July 2024), with normalized electricity consumption in the cement industries (black line) in 2019.</p>
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<p>Daily emission patterns of PM<sub>2.5</sub>, SO<sub>2</sub>, and NO<sub>x</sub> from the cement industry in China’s Tangshan City for the year 2019.</p>
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<p>Hourly PM<sub>2.5</sub> emission patterns in different seasons from clinker production enterprises (<b>a</b>,<b>c</b>,<b>e</b>,<b>g</b>) and separate cement grinding stations (<b>b</b>,<b>d</b>,<b>f</b>,<b>h</b>) in China’s Tangshan City for the year 2019 (spring: February–April; summer: May–July; autumn: August–October; winter: November–January).</p>
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<p>Comparisons of hourly simulation concentrations of PM<sub>2.5</sub> (<b>a</b>), SO<sub>2</sub> (<b>b</b>), and NO<sub>2</sub> (<b>c</b>) based on the optimized emission inventory estimated in this study (optimized simulation) and the traditional emission inventory published by the MEIC (original simulation) (note: the corresponding performance statistics are shown in (<b>d</b>)).</p>
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<p>Detailed information for the study areas and the locations of 83 cement industries.</p>
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<p>Methodology framework for preprocessing EPBD and estimating hourly resolved facility-level air pollutant emissions of cement industries in Tangshan City, China.</p>
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17 pages, 7131 KiB  
Article
Analysis of the Causes of an O3 Pollution Event in Suqian on 18–21 June 2020 Based on the WRF-CMAQ Model
by Ju Wang, Wei Zhang, Weihao Shi, Xinlong Li and Chunsheng Fang
Atmosphere 2024, 15(7), 831; https://doi.org/10.3390/atmos15070831 - 11 Jul 2024
Viewed by 541
Abstract
In recent years, O3 pollution events have occurred frequently in Chinese cities. Utilizing the WRF-CMAQ model, this study analyzed the causes of an O3 pollution event in Suqian on 18–21 June 2020, considering meteorological conditions, process analysis, and source analysis. It [...] Read more.
In recent years, O3 pollution events have occurred frequently in Chinese cities. Utilizing the WRF-CMAQ model, this study analyzed the causes of an O3 pollution event in Suqian on 18–21 June 2020, considering meteorological conditions, process analysis, and source analysis. It also designed 25 emission reduction scenarios to explore more effective O3 emission reduction strategies. The results show that meteorological conditions such as temperature and wind field play an important role in the formation and accumulation of O3. During the heavy pollution period, the contribution of vertical transport (VTRA) and horizontal transport (HTRA) to O3 concentration is significantly enhanced. The photochemical reactions of precursors, such as NOx and VOCs transported from long distances and O3 directly transported to Suqian from other regions, contribute greatly to O3 pollution in Suqian; local sources contribute very little, between 12.22% and 18.33%. Based on the simulation of 25 emission reduction scenarios, it was found that excessive emission reduction of NOx is not conducive to the reduction of O3 concentration, and it is best to control the emission reduction ratio at about 10%. Without affecting normal production and life, it is recommended to reduce VOCs as much as possible, particularly those generated by traffic sources. Full article
(This article belongs to the Special Issue Ozone Pollution and Effects in China)
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<p>Triple-nested map of the WRF-CMAQ model (green triangles represent air quality monitoring stations, green circles represent a meteorological station).</p>
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<p>Time series of monitored (black line) and simulated (red line) T2, WS10, WD10, and O<sub>3</sub> in June 2020.</p>
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<p>Spatial distribution of O<sub>3</sub> (μg/m<sup>3</sup>) at 00:00, 04:00, 08:00, 12:00, 16:00, and 20:00 on 18–21 June 2020 in Suqian.</p>
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<p>Spatial distribution of T2 (°C) at 00:00, 04:00, 08:00, 12:00, 16:00, and 20:00 on 18–21 June 2020 in Suqian.</p>
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<p>Spatial distribution of WS10 (m/s) at 00:00, 04:00, 08:00, 12:00, 16:00, and 20:00 on 18–21 June 2020 in Suqian.</p>
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<p>Surface weather chart in Suqian at 14:00 on 18–21 June 2020 (The blue H represents high pressure and the red L represents low pressure).</p>
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<p>Daily variation chart of the contribution of HTRA, VTRA, CHEM, and DDEP to surface O<sub>3</sub>, including the daily variation of O<sub>3</sub> concentration and net O<sub>3</sub> production in Suqian on (<b>a</b>) 18 June 2020, (<b>b</b>) 19 June 2020, (<b>c</b>) 20 June 2020, and (<b>d</b>) 21 June 2020.</p>
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<p>Daily average variation chart of the contribution of HTRA, VTRA, CHEM, and DDEP to O<sub>3</sub> at different heights, including net O<sub>3</sub> production in Suqian on (<b>a</b>) 18 June 2020, (<b>b</b>) 19 June 2020, (<b>c</b>) 20 June 2020, and (<b>d</b>) 21 June 2020.</p>
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<p>Regional source analysis diagram of O<sub>3</sub> in Suqian in June 2020, including seven parts: the boundary condition (BCON), other unlabeled regions (OTH), Shuyang County (SHY), Sucheng District (SC), Siyang County (SY), Sihong County (SH), and Suyu District (SYU).</p>
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<p>Industry source analysis diagram of O<sub>3</sub> in Suqian in June 2020, including four sectors: the transportation sector (TS), industrial sector (IS), power sector (PS), and residential sector (RS).</p>
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<p>Spatial distribution of the difference in average O<sub>3</sub> concentration (μg/m<sup>3</sup>) between the 25 emission reduction scenarios and the basic scenario at 16:00 on 18–21 June 2020 in Suqian.</p>
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20 pages, 6696 KiB  
Article
Impact of Meteorological Conditions on PM2.5 Pollution in Changchun and Associated Health Risks Analysis
by Chunsheng Fang, Xinlong Li, Juan Li, Jiaqi Tian and Ju Wang
Atmosphere 2024, 15(5), 616; https://doi.org/10.3390/atmos15050616 - 20 May 2024
Cited by 1 | Viewed by 934
Abstract
The escalating concern regarding increasing air pollution and its impact on the health risks associated with PM2.5 in developing countries necessitates attention. Thus, this study utilizes the WRF-CMAQ model to simulate the effects of meteorological conditions on PM2.5 levels in Changchun, [...] Read more.
The escalating concern regarding increasing air pollution and its impact on the health risks associated with PM2.5 in developing countries necessitates attention. Thus, this study utilizes the WRF-CMAQ model to simulate the effects of meteorological conditions on PM2.5 levels in Changchun, a typical city in China, during January 2017 and January 2020. Additionally, it introduces a novel health risk-based air quality index (NHAQI) to assess the influence of meteorological parameters and associated health risks. The findings indicate that in January 2020, the 2-m temperature (T2), 10-m wind speed (WS10), and planetary boundary layer height (PBLH) were lower compared to those in 2017, while air pressure exhibited a slight increase. These meteorological parameters, characterized by reduced wind speed, heightened air pressure, and lower boundary layer height—factors unfavorable for pollutant dispersion—collectively contribute to the accumulation of PM2.5 in the atmosphere. Moreover, the NHAQI proves to be more effective in evaluating health risks compared to the air quality index (AQI). The annual average decrease in NHAQI across six municipal districts from 2017 to 2020 amounts to 18.05%. Notably, the highest health risks are observed during the winter among the four seasons, particularly in densely populated areas. The pollutants contributing the most to the total excess risk (ERtotal) are PM2.5 (45.46%), PM10 (33.30%), and O3 (13.57%) in 2017, and PM2.5 (67.41%), PM10 (22.32%), and O3 (8.41%) in 2020. These results underscore the ongoing necessity for PM2.5 emission control measures while emphasizing the importance of considering meteorological parameters in the development of PM2.5 reduction strategies. Full article
(This article belongs to the Section Air Quality and Health)
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<p>Study area (green circles shown atmospheric monitoring stations; red triangular represents meteorological stations, KC: Kuancheng District, LY: Lvyuan District, CY: Chaoyang District, NG: Nanguan District, ED: Erdao District, SY: Shuangyang District).</p>
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<p>Simulation results of WRF meteorological parameters in Changchun in 2017 and 2020 (2017 on the <b>left</b>, 2020 on the <b>right</b>).</p>
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<p>Box plot of daily average PM<sub>2.5</sub> values in Changchun, January 2017–2020.</p>
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<p>CMAQ simulation results for each monitoring station in Changchun City in January 2017 and 2020 (2017 on the <b>left</b>, 2020 on the <b>right</b>).</p>
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<p>T2 (<b>a</b>), WS10 (<b>b</b>), and Wind Rose of Changchun (<b>c</b>: <b>left</b>: 2017, <b>right</b>: 2020) in January from 2017 to 2020 in Changchun.</p>
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<p>AP (<b>a</b>) and PBLH (<b>b</b>) in January from 2017 to 2020 in Changchun.</p>
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<p>Annual average mass concentrations of six pollutants in Changchun in 2017 and 2020 (The left y-axis is applicable to PM<sub>2.5</sub>, PM<sub>10</sub>, SO<sub>2</sub>, NO<sub>2</sub>, and O<sub>3</sub>, and the right y-axis is applicable to CO).</p>
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<p>Percentage of days in six AQI health categories in Changchun in 2017 and 2020.</p>
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<p>Hourly change in air quality index in Changchun in 2017 and 2020.</p>
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<p>Distribution of NHAQI days in each category for 2017 and 2020 based on AQI health category determination.</p>
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<p>Spatial distribution of four-season NHAQI in Changchun city districts in 2017 and 2020 (KC: Kuancheng District, LY: Lvyuan District, CY: Chaoyang District, NG: Nanguan District, ED: Erdao District, SY: Shuangyang District).</p>
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<p>Average Total Excess Health Risk Values for Changchun City in 2017 and 2020.</p>
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24 pages, 7888 KiB  
Article
Analyses and Simulations of PM2.5 Pollution Characteristics under the Influence of the New Year’s Day Effects in China
by Qiao Shi, Tangyan Hou, Chengli Wang, Zhe Song, Ningning Yao, Yuhai Sun, Boqiong Jiang, Pengfei Li, Zhibin Wang and Shaocai Yu
Atmosphere 2024, 15(5), 568; https://doi.org/10.3390/atmos15050568 - 3 May 2024
Viewed by 1206
Abstract
Regional haze often occurs after the New Year holiday. To explore the characteristics of PM2.5 pollutions under the influence of the New Year’s Day effect, this study analyzed the spatiotemporal changes relating to PM2.5 during and around the New Year’s Day [...] Read more.
Regional haze often occurs after the New Year holiday. To explore the characteristics of PM2.5 pollutions under the influence of the New Year’s Day effect, this study analyzed the spatiotemporal changes relating to PM2.5 during and around the New Year’s Day holiday in China from 2015 to 2022, and used the Weather Research and Forecasting-Community Multiscale Air Quality (WRF-CMAQ) model to study the effects of human activities and meteorological factors on PM2.5 pollutions, as well as the differences in the contributions of different industries to PM2.5 pollutions. The results show that for the entire study period (i.e., before, during, and after the New Year’s Day holiday) from 2015 to 2022, the average concentrations of PM2.5 in China decreased by 41.9% overall. In 2019~2022, the New Year’s Day effect was significant, meaning that the average concentrations of PM2.5 increased by 18.9~46.8 μg/m3 from before to after the New Year’s Day holiday, with its peak occurring (64.3~74.9 μg/m3) after the holiday. In terms of spatial differences, the average concentrations of PM2.5 were higher in the Beijing–Tianjin–Hebei region, the Yangtze River Delta, and central China. Moreover, the Beijing–Tianjin–Hebei region and its surrounding areas, the Chengdu–Chongqing region, the Fenwei Plain, and the middle reaches of the Yangtze River region were greatly affected by the New Year’s Day effect. Human activities led to higher increases in PM2.5 in Henan, Hubei, Hebei, and Anhui on 3 and 4 January 2022. If the haze was accompanied by cloudy days or weak precipitation, the accumulation of surface water vapor and atmospheric aerosols further increased the possibility of heavy pollution. It was found that, for the entire study period, PM2.5 generated by residential sources contributed the vast majority (60~100 μg/m3) of PM2.5 concentrations, and that the main industry sources that caused changes in time distributions were industrial and transportation sources. Full article
(This article belongs to the Section Air Quality)
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<p>(<b>a</b>) Classification of study areas represented by different colors. Beijing–Tianjin–Hebei region and its surrounding areas (BTHS), Yangtze River Delta region (YRD), Fenwei Plain (FWP), Chengdu–Chongqing region (CDCQ), middle reaches of the Yangtze River region (MYRD), Pearl River Delta region (PRD), Northeast region (NE), Southern Coastal region (SC), and Southwest and Northwest region (SWNW). (<b>b</b>) The simulation area of the model, with the outermost layer being the simulation area of WRF and the CMAQ simulation area within the red box.</p>
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<p>The technical roadmap. The results are represented by blue boxes and fonts, with green representing the methods, tools, or data used.</p>
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<p>Changes in the average PM<sub>2.5</sub> concentrations nationwide for the entire study time (i.e., before, during, and after the New Year’s Day holiday) from 2015 to 2022. BDANY: before, during, and after the New Year’s Day holiday. BNY: before the New Year’s Day holiday. DNY: during the New Year’s Day holiday. ANY: after the New Year’s Day holiday.</p>
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<p>The difference in the average PM<sub>2.5</sub> concentration nationwide for the entire study time (i.e., before, during, and after the New Year’s Day holiday) in 2016 and 2022. BDANY: before, during, and after the New Year’s Day holiday. BNY: before the New Year’s Day holiday. DNY: during the New Year’s Day holiday. ANY: after the New Year’s Day holiday. The dots represent the observed values of the corresponding areas.</p>
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<p>Temporal and spatial distributions of the simulated PM<sub>2.5</sub> concentrations in the eastern region, as determined using different emission inventories before the New Year holiday (clean period, first 8 images), for during and after the New Year holiday (pollution period, last 10 images). The dots represent the observed values of the corresponding areas.</p>
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<p>Comparison of simulated and observed values of PM<sub>2.5</sub> using different emission inventories in 22 cities. OBS: observed data. Case16: values simulated using the 2016 emission inventory. Case17: values simulated using the 2017 emission inventory.</p>
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<p>Spatiotemporal distribution maps of simulated differences in PM<sub>2.5</sub> between Case16 (using the 2016 emission inventory) and Case17 (using the 2017 emission inventory) in the eastern region.</p>
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<p>The increases (Case16–Case17) and percentage increases ((Case16–Case17)/Case17) in PM<sub>2.5</sub> concentrations in 12 heavily polluted cities (Jinan, Taiyuan, Zhengzhou, Luoyang, Nanyang, Xinyang, Jiaozuo, Luohe, Xiangyang, Jingzhou, Liaocheng, and Heze).</p>
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<p>The evolution of near-surface temperature (shadow, °C), wind fields (arrow, m/s), and sea level pressures (contour line, hPa) at 08:00 from 30 December 2021 to 5 January 2022.</p>
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<p>The daily average contributions of PM<sub>2.5</sub> by different sources in the eastern region from 30 December 2021 to 5 January 2022. AGR: agricultural source. IND: industrial source. ENE: energy source. RES: residential source. TRA: transportation source.</p>
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14 pages, 5522 KiB  
Article
Analysis of Emission Reduction Measures and Simulation of PM2.5 Concentrations in the Main Cotton Production Areas of Xinjiang in 2025
by Chunsheng Fang, Zhuoqiong Li, Xiao Liu, Weihao Shi, Dali Wang and Ju Wang
Atmosphere 2024, 15(2), 201; https://doi.org/10.3390/atmos15020201 - 5 Feb 2024
Cited by 1 | Viewed by 1002
Abstract
Cotton production in Xinjiang is increasing year by year, and the improved crop yields have had an impact on the environment. This study investigated the changes in six significant pollutants (PM2.5, PM10, SO2, NO2, O [...] Read more.
Cotton production in Xinjiang is increasing year by year, and the improved crop yields have had an impact on the environment. This study investigated the changes in six significant pollutants (PM2.5, PM10, SO2, NO2, O3, and CO) from 2017 to 2022 in Xinjiang. We compiled a biomass burning emission inventory to make the MEIC emission inventory more complete. The Weather Research and Forecasting Community Multiscale Air Quality (WRF–CMAQ) model was employed to simulate air quality in different reduction scenarios in 2025, and it explored ways to alleviate air pollution in the main cotton areas of Xinjiang. The result shows that the main pollutant in Xinjiang is particulate matter (PM particles with aerodynamic diameters less than 2.5 µm and 10 µm), and the concentration of particulate matter decreased from the northern mountains toward the south. The concentrations of O3 (ozone) were highest in summer, while the concentrations of other pollutants were high in autumn and winter. If the pollution is not strictly controlled in terms of emission reduction, it is impossible to achieve the target of a 35 μg/m3 PM2.5 concentration in the planting area. In the scenario of enhanced emission reduction measures and the scenario of higher intensity emission reduction measures, there was a failure to reach the target, despite the reduction in the PM2.5 concentration. In the best emission reduction scenario, PM2.5 in Xinjiang is expected to drop to 22.5 μg/m3 in November and 34 μg/m3 in March, respectively. Therefore, in the optimal emission reduction scenario, the target of 35 μg/m3 will be reached. This study emphasized the importance of future air pollution mitigation and identified a feasible pathway to achieve the target of 35 μg/m3 PM2.5 concentration by 2025. The research findings provide useful insights for the local government which can be used to develop strategies aimed at mitigating substantial pollution emissions. Full article
(This article belongs to the Section Air Quality)
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<p>Model modeling domain, national environmental quality monitoring stations, meteorological stations, and the cotton cultivation areas in Xinjiang.</p>
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<p>Annual average and monthly concentrations of s ix pollutants in Xinjiang from 2017 to 2022.</p>
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<p>Spatial distribution map of six pollutants in Xinjiang Autonomous Region from 2017 to 2022 (unit of CO: mg/m<sup>3</sup>, other units: μg/m<sup>3</sup>).</p>
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<p>Comparison of T<sub>2</sub> and WS<sub>10</sub> simulated and observed values.</p>
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<p>Comparison of T<sub>2</sub> and WS<sub>10</sub> simulated and observed values.</p>
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<p>Comparison of PM<sub>2.5</sub> simulated and observed value.</p>
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<p>Estimated average industry emissions of SO<sub>2</sub>, NO<sub>2</sub>, and PM<sub>2.5</sub> for March and November 2025.</p>
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<p>Spatial distribution of monthly average PM<sub>2.5</sub> concentrations in BAS, EER, SER, and BAT scenarios in March and November 2025.</p>
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<p>Spatial distribution of monthly average PM<sub>2.5</sub> concentrations in BAS, EER, SER, and BAT scenarios in March and November 2025.</p>
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23 pages, 6053 KiB  
Article
The WRF-CMAQ Simulation of a Complex Pollution Episode with High-Level O3 and PM2.5 over the North China Plain: Pollution Characteristics and Causes
by Xuedan Dou, Shaocai Yu, Jiali Li, Yuhai Sun, Zhe Song, Ningning Yao and Pengfei Li
Atmosphere 2024, 15(2), 198; https://doi.org/10.3390/atmos15020198 - 4 Feb 2024
Cited by 1 | Viewed by 1542
Abstract
The problem of atmospheric complex pollution led by PM2.5 and O3 has become an important factor restricting the improvement of air quality in China. In drawing on observations and Weather Research and Forecasting-Community Multiscale Air Quality (WRF-CMAQ) model simulations, this study [...] Read more.
The problem of atmospheric complex pollution led by PM2.5 and O3 has become an important factor restricting the improvement of air quality in China. In drawing on observations and Weather Research and Forecasting-Community Multiscale Air Quality (WRF-CMAQ) model simulations, this study analyzed the characteristics and causes of a regional PM2.5-O3 complex pollution episode in North China Plain, in the period from 3 to 5 April 2019. The results showed that in static and stable weather conditions with high temperature and low wind speed, despite photochemical reactions of O3 near the ground being weakened by high PM2.5 concentrations, a large amount of O3 generated through gas-phase chemical reactions at high altitudes was transported downwards and increased the O3 concentrations at the ground level. The high ground-level O3 could facilitate both the conversion of SO2 and NO2 into secondary inorganic salts and volatile organic compounds into secondary organic aerosols, thereby amplifying PM2.5 concentrations and exacerbating air pollution. The contributions of transport from outside sources to PM2.5 (above 60%) and O3 (above 46%) increased significantly during the episode. This study will play an instrumental role in helping researchers to comprehend the factors that contribute to complex pollution in China, and also offers valuable references for air pollution management. Full article
(This article belongs to the Special Issue Advances in Urban Air Pollution Observation and Simulation)
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<p>The model simulation domain and the simulations with observations overlaid (circle) for (<b>a</b>) PM<sub>2.5</sub> daily average concentrations, (<b>b</b>) MDA8_O<sub>3</sub> concentrations over mainland China from 3 to 5 April 2019. The tracked source regions are shown in (<b>c</b>). BJ: Beijing; TJ: Tianjin; SX: Shanxi; SD: Shandong; HB: Hebei; HN: Henan; HUB: Hubei; AH: Anhui; JS: Jiangsu; OTH: Other regions, except the marked areas in the domain. (<b>d</b>) The geographical distributions of 4 cities in the NCP region (including Handan, Jining, Anyang, Kaifeng).</p>
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<p>Step-by-step workflow.</p>
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<p>Time series of the observed (Obs) and simulated (Sim) T, RH, Wind, PM<sub>2.5</sub>, and O<sub>3</sub> in the four cities from 00:00 LT 30 March to 00:00 LT 10 April 2019. The PM<sub>2.5</sub>-O<sub>3</sub> complex pollution episode was marked by the grey backgrounds.</p>
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<p>Ground weather situation at 8:00 LT from 3 to 5 April 2019. The left column is the ground weather map, and the right column is the ground temperature and wind field map.</p>
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<p>(<b>a</b>) Hourly contributions of CHEM, DDEP, HTRA, and VTRA to O<sub>3</sub> formation in the four cities, with green and pink lines presenting the net O<sub>3</sub> (the sum of all processes) and O<sub>3</sub> concentration changes, respectively. Vertical profiles of (<b>b</b>) daytime (7:00~18:00) and (<b>c</b>) nighttime (17:00~23:00) mean process contributions to the O<sub>3</sub> formation at different heights, from 3 to 5 April 2019.</p>
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<p>Average daily changes of meteorological parameters and pollutant concentrations in Handan, Jining, Anyang and Kaifeng, from 3 to 5 April 2019.</p>
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<p>Time series of O<sub>3</sub> regional source analyses in Handan, Jining, Anyang and Kaifeng, from 31 March to 5 April 2019.</p>
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<p>The spatial distributions of the contributions of different areas to the mean O<sub>3</sub> concentrations, from 3 to 5 April 2019.</p>
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<p>Time series of PM<sub>2.5</sub> regional source analyses in Handan, Jining, Anyang and Kaifeng from 31 March to 5 April 2019.</p>
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<p>The spatial distributions of different area contributions to mean PM<sub>2.5</sub> concentrations, from 3 to 5 April 2019.</p>
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11 pages, 979 KiB  
Article
Forecast of Fine Particles in Chengdu under Autumn–Winter Synoptic Conditions
by Jingchao Yang, Ge Wang and Chao Zhang
Toxics 2023, 11(9), 777; https://doi.org/10.3390/toxics11090777 - 13 Sep 2023
Viewed by 1013
Abstract
We conducted an evaluation of the impact of meteorological factor forecasts on the prediction of fine particles in Chengdu, China, during autumn and winter, utilizing the European Cooperation in Science and Technology (COST)733 objective weather classification software and the Community Multiscale Air Quality [...] Read more.
We conducted an evaluation of the impact of meteorological factor forecasts on the prediction of fine particles in Chengdu, China, during autumn and winter, utilizing the European Cooperation in Science and Technology (COST)733 objective weather classification software and the Community Multiscale Air Quality model. This analysis was performed under four prevailing weather patterns. Fine particle pollution tended to occur under high-pressure rear, homogeneous-pressure, and low-pressure conditions; by contrast, fine particle concentrations were lower under high-pressure bottom conditions. The forecasts of fine particle concentrations were more accurate under high-pressure bottom conditions than under high-pressure rear and homogeneous-pressure conditions. Moreover, under all conditions, the 24 h forecast of fine particle concentrations were more accurate than the 48 and 72 h forecasts. Regarding meteorological factors, forecasts of 2 m relative humidity and 10 m wind speed were more accurate under high-pressure bottom conditions than high-pressure rear and homogeneous-pressure conditions. Moreover, 2 m relative humidity and 10 m wind speed were important factors for forecasting fine particles, whereas 2 m air temperature was not. Finally, the 24 h forecasts of meteorological factors were more accurate than the 48 and 72 h forecasts, consistent with the forecasting of fine particles. Full article
(This article belongs to the Section Air Pollution and Health)
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<p>(<b>a</b>) The domains of the WRF and CMAQ models. The red dot indicates the position of Chengdu, China; (<b>b</b>) spatial distributions of environmental monitoring stations (red dots) and meteorological stations (green dots) in Chengdu.</p>
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<p>Spatial distributions of sea level pressure (SLP; hPa) and 10 m wind fields (m/s) in Chengdu during autumn–winter in 2018–2022 under the four dominant weather patterns: (<b>a</b>) high-pressure rear; (<b>b</b>) high-pressure bottom; (<b>c</b>) homogeneous-pressure; and (<b>d</b>) low-pressure conditions.</p>
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<p>Evaluations of the 24, 48, and 72 h forecasts of daily fine particle concentrations in Chengdu during the period of 1 November 2021 to 28 February 2022 under the four dominant weather patterns (① high-pressure rear, ② high-pressure bottom, ③ homogeneous pressure, and ④ low pressure) based on the AQI: (<b>a</b>) good; (<b>b</b>) moderate; (<b>c</b>) unhealthy for sensitive groups; (<b>d</b>) unhealthy; and (<b>e</b>) very unhealthy.</p>
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16 pages, 4024 KiB  
Article
Development and Application of a Novel Snow Peak Sighting Forecast System over Chengdu
by Chengwei Lu, Ting Chen, Xinyue Yang, Qinwen Tan, Xue Kang, Tianyue Zhang, Zihang Zhou, Fumo Yang, Xi Chen and Yuancheng Wang
Atmosphere 2023, 14(7), 1181; https://doi.org/10.3390/atmos14071181 - 21 Jul 2023
Viewed by 1193
Abstract
As air quality has improved rapidly in recent years, the public has become more interested in whether a famous snow peak, Yaomei Feng on the Tibetan Plateau, can be seen from Chengdu, a megacity located on the western plain of the Sichuan Basin, [...] Read more.
As air quality has improved rapidly in recent years, the public has become more interested in whether a famous snow peak, Yaomei Feng on the Tibetan Plateau, can be seen from Chengdu, a megacity located on the western plain of the Sichuan Basin, east of the plateau. Therefore, a threshold-method-based forecasting system for snow peak sighting was developed in this study. Variables from numerical models, including cloud–water mixing ratio, cloud cover over snow peak, water mixing ratio, PM2.5 concentration, and ground solar radiation, were used in the snow peak sighting forecast system. Terrain occlusion rate of each model grid was calculated. Monte Carlo simulations were applied for threshold determination. A WRF-CMAQ hindcast was conducted for 2020, owing to insufficient observation data, hindcast results on the snow peak sighting were compared with posts collected from social media. Estimations showed that the snow peak sighting forecast system performed well in reflecting the monthly trend of snow peak sightings, and the hindcast results matched the daily observations, especially from May to August. Accuracy of the snow peak sighting forecast model was 78.9%, recall value was 57.1%, and precision was 24.4%. Full article
(This article belongs to the Section Atmospheric Techniques, Instruments, and Modeling)
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<p>Model domain setup, with a photograph of Yaomei Feng taken in Wenjiang District, Chengdu shown in the dashed red box.</p>
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<p>Spatial distribution of air quality and meteorological observing stations.</p>
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<p>Example of terrain occlusion judgment. In the right plot, elevation of the red solid line was shown as the black solid line, the green dashed line showed the sight line from observation point to the peak, and the red dashed line showed the first terrain occlusion height.</p>
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<p>Correlation coefficients distribution of modeled and observed 10 m wind speed, 2 m temperature, atmospheric pressure, and relative humidity for 13 national observation stations.</p>
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<p>Correlation coefficient distribution of modeled and observed NO<sub>2</sub>, O<sub>3</sub>, PM<sub>2.5</sub>, and PM<sub>10</sub> for 35 municipal and national environmental monitoring stations.</p>
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<p>Spatial distribution of terrain occlusion rates.</p>
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<p>Annual spatial distribution of snow peak sighting probability.</p>
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<p>Monthly spatial distribution of snow peak sighting probability.</p>
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<p>Comparisons of modeled and posted snow peak sighting days in months.</p>
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<p>Daily comparison of modeled and posted snow peak sighting.</p>
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28 pages, 5441 KiB  
Article
The Role of Vegetation on Urban Atmosphere of Three European Cities. Part 2: Evaluation of Vegetation Impact on Air Pollutant Concentrations and Depositions
by Mihaela Mircea, Rafael Borge, Sandro Finardi, Gino Briganti, Felicita Russo, David de la Paz, Massimo D’Isidoro, Giuseppe Cremona, Maria Gabriella Villani, Andrea Cappelletti, Mario Adani, Ilaria D’Elia, Antonio Piersanti, Beatrice Sorrentino, Ettore Petralia, Juan Manuel de Andrés, Adolfo Narros, Camillo Silibello, Nicola Pepe, Rossella Prandi and Giuseppe Carlinoadd Show full author list remove Hide full author list
Forests 2023, 14(6), 1255; https://doi.org/10.3390/f14061255 - 16 Jun 2023
Cited by 6 | Viewed by 1605
Abstract
This is the first study that quantifies explicitly the impact of present vegetation on concentrations and depositions, considering simultaneously its effects on meteorology, biogenic emissions, dispersion, and dry deposition in three European cities: Bologna, Milan, and Madrid. The behaviour of three pollutants (O [...] Read more.
This is the first study that quantifies explicitly the impact of present vegetation on concentrations and depositions, considering simultaneously its effects on meteorology, biogenic emissions, dispersion, and dry deposition in three European cities: Bologna, Milan, and Madrid. The behaviour of three pollutants (O3, NO2, and PM10) was investigated considering two different scenarios, with the actual vegetation (VEG) and without it (NOVEG) for two months, representative of summer and winter seasons: July and January. The evaluation is based on simulations performed with two state-of-the-art atmospheric modelling systems (AMS) that use similar but not identical descriptions of physical and chemical atmospheric processes: AMS-MINNI for the two Italian cities and WRF-CMAQ for the Spanish city. The choice of using two AMS and applying one of them in two cities has been made to ensure the robustness of the results needed for their further generalization. The analysis of the spatial distribution of the vegetation effects on air concentrations and depositions shows that they are highly variable from one grid cell to another in the city area, with positive/negative effects or high/low effects in adjacent cells being observed for the three pollutants investigated in all cities. According to the pollutant, on a monthly basis, the highest differences in concentrations (VEG-NOVEG) produced by vegetation were estimated in July for O3 (−7.40 μg/m3 in Madrid and +2.67 μg/m3 in Milan) and NO2 (−3.01 μg/m3 in Milan and +7.17 μg/m3 in Madrid) and in January for PM10 (−3.14 μg/m3 in Milan +2.01 μg/m3 in Madrid). Thus, in some parts of the cities, the presence of vegetation had produced an increase in pollutant concentrations despite its efficient removal action that ranges from ca. 17% for O3 in Bologna (January) to ca. 77% for NO2 in Madrid (July). Full article
(This article belongs to the Section Urban Forestry)
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<p>(<b>a</b>). Monthly sum of emission differences (VEG-NOVEG) for BVOC (upper panel), isoprene (middle panel), and terpenes (bottom panel) (kg/km<sup>2</sup>) from urban vegetation: Bologna (left column), Milano (central column), and Madrid (right column)—January 2015. (<b>b</b>). As (<b>a</b>) for July.</p>
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<p>(<b>a</b>). Monthly sum of emission differences (VEG-NOVEG) for BVOC (upper panel), isoprene (middle panel), and terpenes (bottom panel) (kg/km<sup>2</sup>) from urban vegetation: Bologna (left column), Milano (central column), and Madrid (right column)—January 2015. (<b>b</b>). As (<b>a</b>) for July.</p>
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<p>(<b>a</b>). Monthly averages of differences (VEG-NOVEG) of air concentrations (μg/m<sup>3</sup>) for O<sub>3</sub> (upper panel), NO<sub>2</sub> (middle panel), and PM10 (bottom panel) in Bologna (left column), Milano (central column), and Madrid (right column)—January 2015. (<b>b</b>). As (<b>a</b>) for July.</p>
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<p>(<b>a</b>). Monthly averages of differences (VEG-NOVEG) of air concentrations (μg/m<sup>3</sup>) for O<sub>3</sub> (upper panel), NO<sub>2</sub> (middle panel), and PM10 (bottom panel) in Bologna (left column), Milano (central column), and Madrid (right column)—January 2015. (<b>b</b>). As (<b>a</b>) for July.</p>
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<p>(<b>a</b>). Monthly sum of differences (VEG-NOVEG) of dry depositions (kg/km<sup>2</sup>) for O<sub>3</sub> (upper panel), NO<sub>2</sub> (middle panel), and PM10 (bottom panel) in Bologna (left column), Milan (central column), and Madrid (right column)—January 2015. (<b>b</b>). As (<b>a</b>) for July.</p>
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<p>(<b>a</b>). Monthly sum of differences (VEG-NOVEG) of dry depositions (kg/km<sup>2</sup>) for O<sub>3</sub> (upper panel), NO<sub>2</sub> (middle panel), and PM10 (bottom panel) in Bologna (left column), Milan (central column), and Madrid (right column)—January 2015. (<b>b</b>). As (<b>a</b>) for July.</p>
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<p>Daily cycle of concentrations (mg/m<sup>3</sup>) (upper panels) and depositions (kg/km<sup>2</sup>) (lower panels) differences (VEG-NOVEG) evaluated over urban and vegetation grid cells, considering only grid points inside the municipalities. Rows: O<sub>3</sub>, NO<sub>2,</sub> and PM10 concentrations and depositions. Columns: Bologna, Milan, and Madrid from left to right. Medians are shown as lines, and the shaded area covers the interval 10th to 90th percentiles. Red and blue colours refer to July and January, respectively.</p>
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<p>Daily cycle of concentrations (mg/m<sup>3</sup>) (upper panels) and depositions (kg/km<sup>2</sup>) (lower panels) differences (VEG-NOVEG) evaluated over urban and vegetation grid cells, considering only grid points inside the municipalities. Rows: O<sub>3</sub>, NO<sub>2,</sub> and PM10 concentrations and depositions. Columns: Bologna, Milan, and Madrid from left to right. Medians are shown as lines, and the shaded area covers the interval 10th to 90th percentiles. Red and blue colours refer to July and January, respectively.</p>
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17 pages, 3948 KiB  
Article
Modeling of Organic Aerosol in Seoul Using CMAQ with AERO7
by Hyeon-Yeong Park, Sung-Chul Hong, Jae-Bum Lee and Seog-Yeon Cho
Atmosphere 2023, 14(5), 874; https://doi.org/10.3390/atmos14050874 - 16 May 2023
Cited by 5 | Viewed by 1897
Abstract
The Community Multiscale Air Quality (CMAQ) model with the 7th generation aerosol module (AERO7) was employed to simulate organic aerosol (OA) in Seoul, Korea, for the year 2016. The goal of the present study includes the 1-year simulation of OA using WRF-CMAQ with [...] Read more.
The Community Multiscale Air Quality (CMAQ) model with the 7th generation aerosol module (AERO7) was employed to simulate organic aerosol (OA) in Seoul, Korea, for the year 2016. The goal of the present study includes the 1-year simulation of OA using WRF-CMAQ with recently EPA-developed AERO7 with pcVOC (potential VOC from combustion) scale factor revision and analysis of the seasonal behavior of OA surrogate species in Seoul. The AERO7, the most recent version of the aerosol module of the CMAQ model, includes a new secondary organic aerosol (SOA) species, pcSOA (potential SOA from combustion), to resolve the inherent under-prediction problem of OA. The AERO7 classified OA into three groups: primary organic aerosol (POA), anthropogenic SOA (ASOA), and biogenic SOA (BSOA). Each OA group was further classified into 6~15 individual OA surrogate species according to volatility and oxygen content to model the aging of OA and the formation of SOA. The hourly emissions of POA and SOA precursors were compiled and fed into the CMAQ to successfully simulate seasonal variations of OA compositions and ambient organic-matter to organic-carbon ratios (OM/OC). The model simulation showed that the POA and ASOA were major organic groups in the cool months (from November to March) while BSOA was a major organic group in the warm months (from April to October) in Seoul. The simulated OM/OCs ranged from 1.5~2.1 in Seoul, which agreed well with AMS measurements in Seoul in May 2016. Full article
(This article belongs to the Special Issue Air Quality Prediction and Modeling)
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<p>The study area and the selected PM supersite locations: (<b>a</b>) outer domain, (<b>b</b>) inner domain, (<b>c</b>) BG supersite, and (<b>d</b>) BN supersite.</p>
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<p>Monthly average VOC emissions in the Korea model domain. (<b>a</b>) POA and (<b>b</b>) AVOCs and BVOCs.</p>
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<p>Daily variations of OC, EC, and PM<sub>2.5</sub> concentrations (μg/m<sup>3</sup>) from observation and model in BG supersite. ‘obs’ denotes observation and ‘model’ denotes modeling.</p>
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<p>Daily variations in OC, EC, and PM<sub>2.5</sub> concentrations (μg/m<sup>3</sup>) from observations and modeling in at BN supersite. ‘obs’ denotes observation and ‘model’ denotes modeling.</p>
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<p>Monthly average SOC to POC concentration ratios (SOC/POCs) from observations and modeling. (<b>a</b>) The BG supersite and (<b>b</b>) the BN supersite. ‘obs’ denotes SOC/POCs calculated by the EC tracer method and ‘model’ denotes those calculated by CMAQ.</p>
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<p>Monthly mass composition in Seoul. (<b>a</b>) OA, (<b>b</b>) POA, (<b>c</b>) ASOA, and (<b>d</b>) BSOA. The AIVPO1, ASVOO1, ASVOO2, ASVOO3, AAVB2, AAVB3, AAVB4, and AORGC are not shown in (<b>b</b>–<b>d</b>) due to their negligible mass compositions. In (<b>d</b>), the notation of ‘AMT’ means the sum of AMT1~AMT6, and the percent bars for the cool months were omitted because of negligible BSOA mass concentrations.</p>
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<p>OM to OC ratios (OM/OCs) in Seoul: (<b>a</b>) seasonal variation and (<b>b</b>) diurnal variation. In (<b>a</b>), the OM/OCs of BSOA in the cool months are not shown due to negligible mass concentrations of BSOA.</p>
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15 pages, 3766 KiB  
Article
Analysis of the Impact of Meteorological Factors on Ambient Air Quality during the COVID-19 Lockdown in Jilin City in 2022
by Ju Wang, Weihao Shi, Kexin Xue, Tong Wu and Chunsheng Fang
Atmosphere 2023, 14(2), 400; https://doi.org/10.3390/atmos14020400 - 18 Feb 2023
Cited by 2 | Viewed by 1603
Abstract
This paper explored the changes of six significant pollutants (PM2.5, PM10, SO2, NO2, O3, and CO) in Jilin City during the coronavirus disease 2019 (COVID-19) epidemic in 2022, and compared them with the [...] Read more.
This paper explored the changes of six significant pollutants (PM2.5, PM10, SO2, NO2, O3, and CO) in Jilin City during the coronavirus disease 2019 (COVID-19) epidemic in 2022, and compared them with the same period of previous years to analyze the impact of anthropogenic emissions on the concentration of pollutants; The Weather Research and Forecasting Community Multiscale Air Quality (WRF–CMAQ) model was used to evaluate the effect of meteorological factors on pollutant concentration. The results showed that except for O3, the concentrations of the other five pollutants decreased significantly, with a range of 21–47%, during the lockdown period caused by the government’s shutdown and travel restrictions. Compared with the same period in 2021, the decrease of PM2.5 was only 25% of PM10. That was because there was still a large amount of PM2.5 produced by coal-fired heating during the blockade period, which made the decrease of PM2.5 more minor. A heavy pollution event caused by adverse meteorological conditions was found during the lockdown period, indicating that only controlling artificial emissions cannot eliminate the occurrence of severe pollution events. The WRF–CMAQ results showed that the lower pollutant concentration in 2022 was not only caused by the reduction of anthropogenic emissions but also related to the influence of favorable meteorological factors (higher planetary boundary layer thickness, higher wind speed, and higher temperature). Full article
(This article belongs to the Section Air Quality)
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Figure 1
<p>Simulation domain of the WRF model.</p>
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<p>Comparison of six pollutant concentrations in different years at the same period. (Grey, red, blue, green and purple boxes represent 2018, 2019, 2020, 2021 and 2022 respectively. The diamond represents the outlier, the rectangle represents 25–75% of the data, and the horizontal line in the rectangle represents the median.)</p>
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<p>Variation of daily average concentration of six pollutants. (Purple represents CO, unit: mg/m<sup>3</sup>; Blue represents SO<sub>2</sub>, unit: μg/m<sup>3</sup>; Green represents NO<sub>2</sub>, unit: μg/m<sup>3</sup>; Yellow represents PM<sub>2.5</sub>, unit: μg/m<sup>3</sup>; Red represents O<sub>3</sub>, unit: μg/m<sup>3</sup>; Pink represents PM<sub>10</sub>, unit: μg/m<sup>3</sup>.)</p>
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<p>Hourly changes of six pollutants in different control periods (CO unit: mg/m<sup>3</sup>, other five pollutants unit: μg/m<sup>3</sup>).</p>
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<p>Comparison between T2 analog value and monitoring value.</p>
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<p>Comparison between WS10 analog value and monitoring value.</p>
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<p>Comparison chart of PM<sub>2.5</sub>, PM<sub>10</sub>, NO<sub>2</sub> simulation values, and observation values.</p>
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<p>Correlation between pollutants and meteorological elements.</p>
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