Impacts of weather conditions modified by urban expansion on surface ozone: Comparison between the Pearl River Delta and Yangtze River Delta regions

Wang, Xuemei; Chen, Fei; Wu, Zhiyong; Zhang, Meigen; Tewari, Mukul; Guenther, Alex; Wiedinmyer, Christine

doi:10.1007/s00376-009-8001-2

Cited by 120 publications

(78 citation statements)

References 48 publications

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“…The exacerbation has significant ramifications in terms of public health from both heat and air-quality pathways [6][7][8]. Because of urban heat, the cooling energy demand increases, emissions of anthropogenic and biogenic pollutants (e.g., ozone precursors) increase, the photochemical production of ozone accelerates, and air quality (O 3 , PM 10/2.5 , NO x ) deteriorates [9][10][11][12][13].…”

Section: Introductionmentioning

confidence: 99%

Characterization of Urban Heat and Exacerbation: Development of a Heat Island Index for California

Taha¹

2017

Climate

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Abstract:To further evaluate the factors influencing public heat and air-quality health, a characterization of how urban areas affect the thermal environment, particularly in terms of the air temperature, is necessary. To assist public health agencies in ranking urban areas in terms of heat stress and developing mitigation plans or allocating various resources, this study characterized urban heat in California and quantified an urban heat island index (UHII) at the census-tract level (~1 km 2 ). Multi-scale atmospheric modeling was carried out and a practical UHII definition was developed. The UHII was diagnosed with different metrics and its spatial patterns were characterized for small, large, urban-climate archipelago, inland, and coastal areas. It was found that within each region, wide ranges of urban heat and UHII exist. At the lower end of the scale (in smaller urban areas), the UHII reaches up to 20 degree-hours per day (DH/day; • C.hr/day), whereas at the higher end (in larger areas), it reaches up to 125 DH/day or greater. The average largest temperature difference (urban heat island) within each region ranges from 0.5-1.0 • C in smaller areas to up to 5 • C or more at the higher end, such as in urban-climate archipelagos. Furthermore, urban heat is exacerbated during warmer weather and that, in turn, can worsen the health impacts of heat events presently and in the future, for which it is expected that both the frequency and duration of heat waves will increase.

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Section: Introductionmentioning

confidence: 99%

Characterization of Urban Heat and Exacerbation: Development of a Heat Island Index for California

Taha¹

2017

Climate

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“…WRF-Chem is a state-of-the-art, regional atmospheric chemistry model (Grell et al, 2005) and has been successfully applied for regional air quality studies (Wang et al, 2009). Due to lack of observational data, few studies have evaluated the ability of the WDDM for calculating nitrogen V d , even though dry deposition is one of the most important sinks for pollutants.…”

Section: Introductionmentioning

confidence: 99%

Evaluating the calculated dry deposition velocities of reactive nitrogen oxides and ozone from two community models over a temperate deciduous forest

Wang

Chen

et al. 2011

Atmospheric Environment

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Evaluating the calculated dry deposition velocities of reactive nitrogen oxides and ozone from two community models over a temperate deciduous forest ) is very sensitive to the minimum canopy stomatal resistance (R i ) which is specified for each seasonal category assigned in WDDM. Treating Sep-Oct as autumn in WDDM for this deciduous forest site caused a large underprediction of V d (O 3 ) due to the leafless assumption in 'autumn' seasonal category for which an infinite R i was assigned. Reducing R i to a value of 70 s m À1 , the same as the default value for the summer season category, the modeled and measured V d (O 3 ) agreed reasonably well. HNO 3 was found to dominate the NO y flux during the measurement period; thus the modeled V d (NO y ) was mainly controlled by the aerodynamic and quasi-laminar sublayer resistances (R a and R b ), both being sensitive to the surface roughness length (z 0 ). Using an appropriate value for z 0 (10% of canopy height), WDDM and Noah-GEM agreed well with the observed daytime V d (NO y ). The differences in V d (HNO 3 ) between WDDM and Noah-GEM were small due to the small differences in the calculated R a and R b between the two models; however, the differences in R c of NO 2 and PAN between the two models reached a factor of 1.1e1.5, which in turn caused a factor of 1.1e1.3 differences for V d . Combining the measured concentrations and modeled V d , NO x , PAN and HNO 3 accounted for 19%, 4%, and 70% of the measured NO y fluxes, respectively.

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“…The gas phase chemistry scheme CBM-Z (Zaveri and Peters, 1999) was selected for this study because it can better represent surface ozone that agrees with the observations in the PRD region (Wang et al, 2009). CBM-Z is a new lumped structure photochemical mechanism for large-scale applications.…”

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confidence: 99%

Impacts of seasonal and regional variability in biogenic VOC emissions on surface ozone in the Pearl River delta region, China

et al. 2013

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Abstract. This study investigated the impacts of seasonal and regional variability in biogenic volatile organic compounds (BVOCs) on surface ozone over the Pearl River delta (PRD) region in southern China in 2010 with the WRFChem/MEGAN (Weather Research and Forecasting coupled with Chemistry/Model of Emissions of Gases and Aerosols from Nature) modeling system. Compared to observations in the literature and this study, MEGAN tends to predict reasonable BVOC emissions in summer, but may overestimate isoprene emissions in autumn, even when the local high-resolution land-cover data and observed emission factors of BVOCs from local plant species are combined to constrain the MEGAN BVOC emissions model. With the standard MEGAN output, it is shown that the impact of BVOC emissions on the surface ozone peak is ∼ 3 ppb on average with a maximum of 24.8 ppb over the PRD region in autumn, while the impact is ∼ 10 ppb on average, with a maximum value of 34.0 ppb in summer. The areas where surface ozone is sensitive to BVOC emissions are different in autumn and in summer, which is primarily due to the change of prevailing wind over the PRD; nevertheless, in both autumn and summer, the surface ozone is most sensitive to the BVOC emissions in the urban area because the area is usually VOC-limited. Three additional experiments concerning the sensitivity of surface ozone to MEGAN input variables were also performed to assess the sensitivity of surface ozone to MEGAN drivers, and the results reveal that land cover and emission factors of BVOCs are the most important drivers and have large impacts on the predicted surface ozone.

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Impacts of weather conditions modified by urban expansion on surface ozone: Comparison between the Pearl River Delta and Yangtze River Delta regions

Cited by 120 publications

References 48 publications

Characterization of Urban Heat and Exacerbation: Development of a Heat Island Index for California

Characterization of Urban Heat and Exacerbation: Development of a Heat Island Index for California

Evaluating the calculated dry deposition velocities of reactive nitrogen oxides and ozone from two community models over a temperate deciduous forest

Impacts of seasonal and regional variability in biogenic VOC emissions on surface ozone in the Pearl River delta region, China

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