High aerosol and high ozone pollution and vertical distribution of extinction coefficients in Guangzhou during the dry season
TAO Li-ping1, DENG Tao2, WU Dui1,2, WU Cheng1, HE Guo-wen1, ZHANG Xue1, SONG Lang1, OUYANG Shan-shan3, SUN Jia-yin1, LIANG Yue1, TAN Jian1, XIA Rui1, ZHOU Zhen1
1. Institute of Mass Spectrometry and Atmospheric Environment, Guangdong Engineering Research Centre for Online Atmospheric Pollution Source Appointment Mass Spectrometry System, Jinan University, Guangzhou 510632, China; 2. Guangzhou Institute of Tropical and Marine Meteorology, China Meteorological Administration, Guangzhou 510640, China; 3. Institute for Environmental and Climate Research, Jinan University, Guangzhou 511443, China
Abstract:Based on regular surface observation meteorological data, data of six kinds of air quality parameters, actinic radiation data, aerosol scattering and absorption coefficients, single scattering albedo, and aerosol extinction coefficient and depolarization ratio retrieved by lidar data from December 6, 2017 to January 3, 2018 in Guangzhou, this paper analyzed the influence of meteorological parameters variation on pollutant concentration and actinic radiation attenuation by aerosols, studied the formation mechanism of high aerosol and high ozone (double high) pollution, and explored the evolution of extinction coefficient profile in the vertical direction within the boundary layer on double high days. The actinic radiation attenuation on double high days is less than that on haze days during the study period. The scattering and absorption of aerosols has certain attenuation effect on actinic radiation. The scattering components of aerosols have positive feedback on actinic radiation, and the strong actinic radiation on double high days keeps O3 and PM2.5 concentration at a high level. Compared with non-double high days, double high days feature lower wind speed, higher temperature, stronger actinic radiation, higher PM2.5, CO, SO2, and NO2 concentration, higher fine particle ratio, and higher near-surface depolarization ratio during 11:00-16:00. Radar observation shows that the high value area of extinction coefficient is below 0.5km at 8:00 am on four double high days. The mean value area of extinction coefficient appears in the low layer and keeps rising. Actinic radiation flux abates in the afternoon, and its mean value area no longer develops upwards. Extinction coefficient above the mean value area gradually increases vertically as particulate pollution aggravates, and it peaks near the top of the boundary layer. At night, extinction coefficient reduces with the rise of height at the low altitude, increases with the rise of height within a certain altitude range, and decreases exponentially above 1km. The high value area near the top of the boundary layer is more obvious at night.
陶丽萍, 邓涛, 吴兑, 吴晟, 何国文, 张雪, 宋烺, 欧阳珊珊, 孙嘉胤, 梁粤, 谭健, 夏瑞, 周振. 广州旱季双高污染及消光系数垂直分布特征[J]. 中国环境科学, 2022, 42(2): 497-508.
TAO Li-ping, DENG Tao, WU Dui, WU Cheng, HE Guo-wen, ZHANG Xue, SONG Lang, OUYANG Shan-shan, SUN Jia-yin, LIANG Yue, TAN Jian, XIA Rui, ZHOU Zhen. High aerosol and high ozone pollution and vertical distribution of extinction coefficients in Guangzhou during the dry season. CHINA ENVIRONMENTAL SCIENCECE, 2022, 42(2): 497-508.
Wang X Q, Wei W, Cheng S Y, et al. Characteristics and classification of PM2.5 pollution episodes in Beijing from 2013 to 2015[J]. Science of The Total Environment, 2018,612:170-179.
[2]
Bai Y Q, Zhao T L, Hu W Y, et al. Meteorological mechanism of regional PM2.5 transport building a receptor region for heavy air pollution over Central China[J]. Science of The Total Environment, 2022,808:151951.
[3]
Shen X J, Sun J Y, Zhang X Y, et al. Variations in submicron aerosol liquid water content and the contribution of chemical components during heavy aerosol pollution episodes in winter in Beijing[J]. Science of The Total Environment, 2019,693:133521.
[4]
Wang J F, Ye J H, Zhang Q, et al. Aqueous production of secondary organic aerosol from fossil-fuel emissions in winter Beijing haze[J]. Proceedings of the National Academy of Sciences, 2021,118(8):e2022179118.
[5]
Zhong J T, Zhang X Y, Wang Y Q, et al. The two-way feedback mechanism between unfavorable meteorological conditions and cumulative aerosol pollution in various haze regions of China[J]. Atmos. Chem. Phys., 2019,19(5):3287-3306.
[6]
Zhang T, Che H Z, Gong Z Q, et al. The two-way feedback effect between aerosol pollution and planetary boundary layer structure on the explosive rise of PM2.5 after the "Ten Statements of Atmosphere" in Beijing[J]. Science of The Total Environment, 2020,709:136259.
[7]
Zhang X Y, Xu X D, Ding Y H, et al. The impact of meteorological changes from 2013 to 2017 on PM2.5 mass reduction in key regions in China[J]. Science China Earth Sciences, 2019:1-18.
[8]
Chen B, Song Z H, Pan F, et al. Obtaining vertical distribution of PM2.5 from CALIOP data and machine learning algorithms[J]. Science of The Total Environment, 2022,805:150338.
[9]
Li K, Jacob D J, Liao H, et al. Ozone pollution in the North China Plain spreading into the late-winter haze season[J]. Proceedings of the National Academy of Sciences, 2021,118(10):e2015797118.
[10]
Dang R J, Liao H, Fu Y. Quantifying the anthropogenic and meteorological influences on summertime surface ozone in China over 2012-2017[J]. Sci. Total Environ., 2021,754:142394.
[11]
Wang Y, Zhang Y, Hao J, et al. Seasonal and spatial variability of surface ozone over China:contributions from background and domestic pollution[J]. Atmos. Chem. Phys., 2011,11(7):3511-3525.
[12]
Liu X F, Wang N, Lyu X P, et al. Photochemistry of ozone pollution in autumn in Pearl River Estuary, South China[J]. Science of The Total Environment, 2021,754:141812.
[13]
Zhu X W, Ma Z Q, Qiu Y L, et al. An evaluation of the interaction of morning residual layer ozone and mixing layer ozone in rural areas of the North China Plain[J]. Atmospheric Research, 2020,236:104788.
[14]
Li X B, Fan G Q, Lou S R, et al. Transport and boundary layer interaction contribution to extremely high surface ozone levels in eastern China[J]. Environmental Pollution, 2021,268:115804.
[15]
He G W, Deng T, Wu D, et al. Characteristics of boundary layer ozone and its effect on surface ozone concentration in Shenzhen, China:A case study[J]. Science of The Total Environment, 2021,791:148044.
[16]
Hu J, Hu X M, Gao L, et al. Impacts of Nocturnal Cloud Top Radiative Cooling on Surface O3 in Sichuan Basin, Southwestern China[J]. Earth and Space Science, 2021,8(3):e2020EA001541.
[17]
Miao Y C, Che H Z, Zhang X Y, et al. Relationship between summertime concurring PM2.5 and O3 pollution and boundary layer height differs between Beijing and Shanghai, China[J]. Environmental Pollution, 2021,268:115775.
[18]
Huang L, Sun J J, Jin L, et al. Strategies to reduce PM2.5 and O3 together during late summer and early fall in San Joaquin Valley, California[J]. Atmospheric Research, 2021,258:105633.
[19]
Jia M W, Zhao T L, Cheng X H, et al. Inverse Relations of PM2.5 and O3 in Air Compound Pollution between Cold and Hot Seasons over an Urban Area of East China[J]. Atmosphere, 2017,8(3):59.
[20]
Yuan T L, Remer L A, Bian H S, et al. Aerosol indirect effect on tropospheric ozone via lightning[J]. Journal of Geophysical Research:Atmospheres, 2012,117:D18213
[21]
Qin M M, Hu A Q, Mao J J, et al. PM2.5 and O3 relationships affected by the atmospheric oxidizing capacity in the Yangtze River Delta, China[J]. Science of The Total Environment, 2022,810:152268.
[22]
Campbell J R, Hlavka D L, Welton E J, et al. Full-Time, Eye-Safe Cloud and Aerosol Lidar Observation at Atmospheric Radiation Measurement Program Sites:Instruments and Data Processing[J]. Journal of Atmospheric and Oceanic Technology, 2002, 19(4):431-442.
[23]
Frederick G F. Analysis of atmospheric Lidar observations:some comments[J]. Applied Optics, 1984,23(5):652-653.
[24]
邓涛,吴兑,邓雪娇,等.一次严重灰霾过程的气溶胶光学特性垂直分布[J]. 中国环境科学, 2013,33(11):1921-1928. Deng T, Wu D, Deng X J, et al. The vertical distribution of aerosol optical properties in a severe haze event[J]. China Environmental Science, 2013,33(11):1921-1928.
[25]
Stein A F, Draxler R R, Rolph G D, et al. NOAA's HYSPLIT Atmospheric Transport and Dispersion Modeling System[J]. Bulletin of the American Meteorological Society, 2015,96(12):2059-2077.
[26]
Parrish D D, Murphy P C, Albritton D L, et al. The measurement of the photodissociation rate of NO2 in the atmosphere[J]. Atmospheric Environment, 1983,17(7):1365-1379.
[27]
Fialho P, Hansen A D A, Honrath R E. Absorption coefficients by aerosols in remote areas:a new approach to decouple dust and black carbon absorption coefficients using seven-wavelength Aethalometer data[J]. Journal of Aerosol Science, 2005,36(2):267-282.
[28]
Poltera Y, Martucci G, Cone M C, et al. Pathfinder TURB:an automatic boundary layer algorithm. Development, validation and application to study the impact on in situ measurements at the Jungfraujoch[J]. Atmos. Chem. Phys., 2017,17(16):10051-10070.
[29]
Boers R, Eloranta E W, Coulter R L. Lidar Observations of Mixed Layer Dynamics:Tests of Parameterized Entrainment Models of Mixed Layer Growth Rate[J]. Journal of Applied Meteorology and Climatology, 1984,23(2):247-266.
[30]
Bachour D, Astudillo P D. Boundary Layer Height Measurements over Doha Using Lidar[J]. Energy Procedia, 2014,57:1086-1091.
[31]
Steyn D G, Baldi M, Hoff R M. The Detection of Mixed Layer Depth and Entrainment Zone Thickness from Lidar Backscatter Profiles[J]. Journal of Atmospheric and Oceanic Technology, 1999,16:953-959.
[32]
Song L, Deng T, Li Z N, et al. Retrieval of Boundary Layer Height and Its Influence on PM2.5 Concentration Based on Lidar Observation over Guangzhou[J]. Journal of Tropical Meteorology, 2021,27(3):303-318.
[33]
GB/T 36542-2018霾的观测识别[S]. GB/T 36542-2018 Haze identification for meteorological observation[S].
[34]
黄俊,廖碧婷,吴兑,等.广州近地面臭氧浓度特征及气象影响分析[J]. 环境科学学报, 2018,38(1):23-31. Huang J, Liao B T, Wu D, et al. Guangzhou ground level ozone concentration characteristics and associated meteorological factors[J]. Acta Scientiae Circumstantiae, 2018,38(1):23-31.
[35]
Tan H B, Yin Y, Li F, et al. Measurements of particle number size distributions and new particle formation events during winter in the Pearl River Delta region, CHINA[J]. Journal of Tropical Meteorology, 2016,22(2):191-199.
[36]
Mai B R, Deng X J, Liu X, et al. Direct Radiative Effect of Aerosols on Net Ecosystem Carbon Exchange in the Pearl River Delta Region[J]. Journal of Tropical Meteorology, 2021,27(3):272-281.
[37]
Deng T, Wang T J, Wang S Q, et al. Impact of typhoon periphery on high ozone and high aerosol pollution in the Pearl River Delta region[J]. Science of The Total Environment, 2019,668:617-630.