J. Meteor. Res.  2017, Vol. 31 Issue (5): 865-873 PDF
http://dx.doi.org/10.1007/s13351-017-7007-4
The Chinese Meteorological Society
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#### Article Information

SUN, Kai, Hongnian LIU, Xueyuan WANG, et al., 2017.
The Aerosol Radiative Effect on a Severe Haze Episode in the Yangtze River Delta. 2017.
J. Meteor. Res., 31(5): 865-873
http://dx.doi.org/10.1007/s13351-017-7007-4

### Article History

in final form June 14, 2017
The Aerosol Radiative Effect on a Severe Haze Episode in the Yangtze River Delta
Kai SUN1, Hongnian LIU1, Xueyuan WANG1, Zhen PENG1, Zhe XIONG2
1. School of Atmospheric Sciences, Nanjing University, Nanjing 210023;
2. Key Laboratory of Climate–Environment for East Asia, Institute of Atmospheric Physics, Chinese Academy of Sciences, Beijing 100029
ABSTRACT: Due to increased aerosol emissions and unfavorable weather conditions, severe haze events have occurred frequently in China in the last 10 years. In addition, the interaction between the boundary layer and the aerosol radiative effect may be another important factor in haze formation. To better understand the effect of this interaction, the aerosol radiative effect on a severe haze episode that took place in December 2013 was investigated by using two WRF-Chem model simulations with different aerosol configurations. The results showed that the maximal reduction of regional average surface shortwave radiation, latent heat, and sensible heat during this event were 88, 12, and 37 W m–2, respectively. The planetary boundary layer height, daytime temperature, and wind speed dropped by 276 m, 1°C, and 0.33 m s–1, respectively. The ventilation coefficient dropped by 8%–24% for in the central and northwestern Yangtze River Delta (YRD). The upper level of the atmosphere was warmed and the lower level was cooled, which stabilized the stratification. In a word, the dispersion ability of the atmosphere was weakened due to the aerosol radiative feedback. Additional results showed that the PM2.5 concentration in the central and northwestern YRD increased by 6–18 μg m–3, which is less than 15% of the average PM2.5 concentration during the severely polluted period in this area. The vertical profile showed that the PM2.5 and PM10 concentrations increased below 950 hPa, with a maximum increase of 7 and 8 μg m–3, respectively. Concentrations reduced between 950 and 800 hPa, however, with a maximum reduction of 3.5 and 4.5 μg m–3, respectively. Generally, the aerosol radiative effect aggravated the level of pollution, but the effect was limited, and this haze event was mainly caused by the stagnant meteorological conditions. The interaction between the boundary layer and the aerosol radiative effect may have been less important than the large-scale static weather conditions for the formation of this haze episode.
Key words: haze     aerosol radiative effect     Yangtze River Delta     ventilation coefficient     PM2.5     WRF-Chem
1 Introduction

Aerosols affect the climate by influencing the energy budget of the earth. This is referred to as the climate effect of aerosols, and many relevant works have been conducted to study this effect (IPCC, 2007; Forkel et al., 2012; Zhao and Garrett, 2015). In the last 10 years, haze events have occurred frequently in China, with extreme aerosol concentrations usually reaching above 200 μg m–3 (Tie and Cao, 2009; Tao et al., 2014; Zhang L. et al., 2015). The influences on meteorological fields imposed by the high concentrations of aerosols during haze events are quite different from those reported by relevant studies focusing on longer time periods, such as one year, which are generally accompanied by lower aerosol concentrations. Firstly, the influences of aerosols on meteorological factors during haze events are obvious. Zhang B. et al. (2015) analyzed a severe haze event in China during January 2013 and found that the surface downward shortwave radiation, 2-m temperature, 10-m wind speed, and planetary boundary layer (PBL) height decreased by 84.0 W m–2, 3.2°C, 0.8 m s–1, and 268 m, respectively. Secondly, changes in meteorological factors during haze events are temporary, and fluctuate widely with variations in pollutant concentrations.

The interaction between high concentrations of aerosols and meteorological fields during haze events mainly include: (i) the changes in meteorological factors such as temperature, wind fields, and PBL height due to aerosol radiative effects, which in turn affect the transport and diffusion of the aerosols themselves (Ding et al., 2013; Yang et al., 2015); and (ii) the attenuation of incoming solar radiation, which affects the photochemical processes of pollutants (Wendisch et al., 2010; Zhang et al., 2010). To date, whilst we have a general understanding of the mechanism involved in the interaction between aerosols and meteorological factors, the specific degree of interaction still needs to be more thoroughly investigated. In particular, how this interaction increases pollutant concentrations during heavy haze events, which then further aggravates the level of pollution, is not well understood. Additionally, relevant findings can effectively improve the accuracy of air quality forecasts (Wang et al., 2013, 2014; Zhang et al., 2014). Therefore, in this study, we selected and simulated a severe haze event that occurred in early December 2013 in the Yangtze River Delta (YRD) to analyze the aerosol radiative effect during various periods of this pollution event.

2 Methodology and data 2.1 Model configuration

Version 3.5.1 of WRF-Chem (Grell et al., 2005) was used for the simulation in this study. The major physics options selected included the Goddard shortwave radiation scheme, the Rapid Radiative Transfer Model longwave radiation scheme (Mlawer et al., 1997), the Fast-J photolysis scheme (Wild et al., 2000), the Noah land-surface module (Chen and Dudhia, 2001), the Yonsei University PBL scheme (Hong et al., 2006), the WRF single moment 5-class cloud microphysics (Hong et al., 2004), and the Grell 3D cumulus parameterization. The gas-phase chemical mechanism adopted was the Regional Acid Deposition Model, version 2 (Stockwell et al., 1990). The modal aerosol dynamics model for Europe (Ackermann et al., 1998) and the secondary organic aerosol model (Schell et al., 2001) were used for the aerosols. For the calculation of biogenic emissions, the model of emissions of gases and aerosols from nature (Guenther et al., 2006) was adopted. For land use, the 1-km moderate resolution imaging spectroradiometer data (Friedl et al., 2002) were employed.

The initial and boundary meteorological conditions were obtained from the NCEP global final (FNL) analysis data, available every 6 h at a grid spacing of 1° × 1°. The chemical initial and boundary conditions were obtained from simulations of the model for ozone and related chemical tracers, version 4, at a resolution of 1.9° × 2.5° (Emmons et al., 2010).

The model adopts three layers of nesting, and the grid resolutions of the outermost (D01), middle (D02), and innermost (D03) layers were 27 km × 27 km, 9 km × 9 km, and 3 km × 3 km, respectively. The D03 layer covered the entire YRD, and the number of grid points was 241 (east–west) × 265 (south–north). The model includes a total of 25 vertical levels, and the pressure at the top of the model was set to 50 hPa. The simulation was initiated at 0000 UTC 27 November 2013 and ended at 0000 UTC 12 December 2013, with data outputted hourly. The first 24 hours of the simulation were discarded as model spin-up time, and thus we began the analysis at 0000 UTC 28 November 2013. A total of 14 days of results were analyzed.

Two experiments were carried out. In the first experiment (Case-1), all aerosol feedbacks were completely switched off; whereas, in the second experiment (Case-2), the direct aerosol radiative effect was included. To compute the optical characteristics of aerosols in Case-2, we used the volume approximation scheme. Except for the difference mentioned above, the other model settings in Case-2 remained the same as in Case-1. The differences between the two sets of simulation results (i.e., Case-2 minus Case-1) were used to identify the influence of the aerosol direct radiative effect on meteorological factors.

An evaluation of the Case-1 simulation against observational data, together with some further analysis of this episode, such as its formation and dissipation processes, the chemical composition of the fine particles, and the pollutants’ spatial distribution, is detailed in another paper (Sun et al., 2016).

2.2 Anthropogenic emissions

In this study, we obtained information on anthropogenic emissions from the Multi-resolution Emission Inventory for China (MEIC; http://www.meicmodel.org; He, 2012), and allocated it vertically in the model using the method of Wang et al. (2010). MEIC is a newly released emissions inventory for China, and its horizontal resolution is 0.25° × 0.25°. It includes emissions information on black carbon, CO, CO2, NH3, NOx, organic carbon, PM2.5, PM10, SO2, and non-methane volatile organic compounds for five sectors (power, industry, residential, transportation, and agriculture). MEIC was developed by the INTEX-B (Intercontinental Chemical Transport Experiment) team at Tsinghua University of China.

3 Results 3.1 Characteristics of the haze episode

We divided the haze event into three periods: Phases 1, 2, and 3, corresponding to the pre-pollution period (0000 UTC 28 to 2300 UTC 30 November), the severely polluted period (0000 UTC 1 to 2300 UTC 8 December), and the post-pollution period (0000 UTC 9 to 2300 UTC 11 December).

Figure 1 shows the spatial distribution of the average PM2.5 concentration in Phase 2. It shows that the PM2.5 concentration was high in the central and northwestern YRD. The average PM2.5 concentration of the urban agglomeration (Nanjing–Suzhou–Shanghai) in the central area of the YRD exceeded 220 μg m–3. The surrounding area of Hefei City, Anhui Province, was also a center of high PM2.5 concentration (> 220 μg m–3), whereas the value was generally above 160 μg m–3 in the vast area of the northwestern YRD (Jiangsu Province and the northern part of Anhui Province).

 Figure 1 Simulated average surface PM2.5 concentration (μg m–3) during the severely polluted period.
3.2 Influence of the aerosol radiative effect on meteorological factors

 Figure 2 Influence of the aerosol radiative effect on average meteorological factors (Case-2 minus Case-1): (a) downward shortwave radiation at the surface (W m–2); (b) upward sensible heat flux (W m–2); (c) latent heat flux (W m–2); (d) PBL height (m); (e) 2-m nighttime temperature (°C); (f) 2-m daytime temperature (°C); (g) 2-m relative humidity (%); and (h) 10-m wind speed (m s–1).

Figure 3 shows the time series for the influence of the aerosol radiative effect on the regional average results, and the selected region is north of 29.5°N in the innermost domain. We can see that, during Phase 2, the downward shortwave radiation, latent heat flux, and sensible heat flux decreased considerably. During 6–7 December, when the aerosol concentration reached its maximum, the downward shortwave radiation, latent heat flux, and sensible heat flux decreased by 88, 12, and 37 W m–2, respectively. Moreover, the daytime temperature decreased by 1°C on 7 December; the boundary layer height decreased by 276 and 263 m on 3 and 6 December, respectively; and the wind speed decreased by 0.33 m s–1 on 8 December. From Fig. 3d, we can see that the wind speed did not vary so closely with the aerosol concentration as other meteorological factors. Generally, the aerosol radiative effect during this haze event caused radiative factors (e.g., surface shortwave radiation, latent heat flux, and sensible heat flux) to decrease, and thus the temperature decreased as a result. The reduction in PBL height and wind speed weakened the ability of the atmosphere to diffuse and dilute pollutants.

 Figure 3 (a) PM2.5 concentration of Case-1. (b–d) Regional average variations (Case-2 minus Case-1) of meteorological factors caused by the aerosol radiative effect: (b) downward shortwave radiation and latent heat; (c) daytime 2-m temperature and sensible heat; (d) PBL height and 10-m wind speed. The land area to the north of 29.5°N in D03 was selected for the calculations.

Figure 4 shows the rate of change (%) in the average ventilation coefficient (VC) due to the aerosol radiative effect during Phase 2. The VC was defined in Sun et al. (2016), and is an indicator of the horizontal dispersion ability of the atmosphere. The lower the VC is, the weaker the ability of the atmosphere has to disperse pollutants horizontally. From Fig. 4, we can see that the VC decreased throughout almost the whole of the YRD, and the reduction in the central and northwestern YRD varied between 8% and 24%, which may have been mainly due to the reduced near-surface wind speed and PBL height.

 Figure 4 Rate of change (i.e., $\frac{{{\rm{Case}}\text{-}2 - {\rm Case}\text{-}1}}{{{\rm{Case}}\text{-}1}} \times 100\%$ ) in the average ventilation coefficient (VC) during Phase 2 due to the aerosol radiative effect.

Figure 5 compares the average vertical temperature profile at Nanjing (32.12°N, 118.95°E) for the two cases. We can see that the temperature of the lower atmosphere decreased, but that of the upper layer increased. This was because the aerosol radiative effect cooled the lower atmosphere and warmed the upper layer via the scattering and absorption effects of aerosols. Generally, the radiative forcing at the surface and the top of the atmosphere due to aerosols is negative, and that of an air column is positive (Liu et al., 2010). In the present case, the effect of warming in the upper layers and cooling in the lower layers further intensified the near-surface temperature inversion shown in Fig. 5, which stabilized the lower atmosphere and thus weakened the vertical transport and diffusion of pollutants.

 Figure 5 Average temperature profile with (dashed line) and without (solid line) the aerosol radiative effect in Nanjing.
3.3 Influence of the aerosol radiative effect on pollutant concentrations

The weakened horizontal and vertical dispersion ability of the atmosphere, together with high relative humidity, which promotes gas-to-particle transformation, are important factors in the aggravation of pollution. Figure 6 shows the difference (Case-2 minus Case-1) in the average surface PM2.5 concentration during Phase 2. From Figs. 4, 6, we can see that, in regions with a large reduction in VC, such as the central and northwestern YRD, the corresponding PM2.5 concentration increased obviously. Figure 6 shows that, in regions with high PM2.5 concentrations during the polluted period (e.g., the central YRD; Fig. 1), the PM2.5 concentration increased by approximately 6–24 μg m–3. However, in comparison with the original (Case-1) high concentration of PM2.5 (160–300 μg m–3), the enhancement was no more than 15%. We believe that this severe haze event was caused by stagnant meteorological conditions that were not conducive to the dispersion of pollutants. The aerosol radiative effect aggravated the level of pollution, but it was not the determining factor for the formation of this haze event.

 Figure 6 Change (Case-2 minus Case-1) in the average PM2.5 concentration (μg m–3) caused by the aerosol radiative effect during Phase 2.

Figure 7 shows the influence of the aerosol radiative effect on the vertical profile of the average pollutant concentration in Nanjing. Below approximately 950 hPa, the PM2.5 and PM10 concentrations increased by up to 7 and 8 μg m–3, respectively, whereas they decreased by up to 3.5 and 4.5 μg m–3 between the levels of 800 and 950 hPa. This probably occurred as the PBL height decreased due to the influence of the aerosol radiative effect, trapping pollutants near the ground surface. In contrast, the O3 concentration decreased by up to 1.1 μg m–3 in the bottom layer of the atmosphere (below 950 hPa), and there was an increase of up to 1.7 μg m–3 between the levels of 950 and 770 hPa. This probably occurred because, as the PBL height decreased, aerosols were trapped near the surface. The higher aerosol concentration at the low level reduced the incoming shortwave radiation below 950 hPa and further decreased the O3 generation rate at this level. On the contrary, at higher levels, with reduced aerosol concentrations, the O3 concentration increased.

 Figure 7 Changes in the average concentration (μg m–3) profiles at Nanjing due to the aerosol radiative effect: (a) PM2.5, (b) PM10, and (c) O3.

In summary, the aerosol radiative effect weakened the dispersion ability of the atmosphere, which to some extent aggravated the level of aerosol pollution. It also changed the vertical distribution of pollutants, and the influence varied among different kinds of pollutants.

4 Summary

In this study, we used the WRF-Chem model to study the aerosol radiative effect of a severe haze event in the YRD in December 2013. The main conclusions are as follows.

(1) The average PM2.5 concentration during Phase 2 in the central (Nanjing–Suzhou–Shanghai urban agglomeration) and northwestern YRD exceeded 220 and 160 μg m–3, respectively. The high aerosol concentration reduced the downward shortwave solar radiation reaching the ground surface in the central and northwestern YRD by 52–65 and 39–65 W m–2, respectively. The daytime and nighttime near-surface temperatures decreased and the cooling effect was more obvious during the day. The maximum reduction in the regional average downward shortwave radiation, latent heat flux, and sensible heat flux was 88, 12, and 37 W m–2, respectively. During the daytime, the maximum decreases in temperature, PBL height, and surface wind speed were 1°C, 276 m, and 0.33 m s–1, respectively. The relative humidity increased by 1%–4%.

(2) Due to the reduction in wind speed and boundary layer height, the VC decreased throughout almost the whole of the YRD. The reduction in the VC was 8%–24% in the central and northwestern YRD.

(3) In terms of horizontal dispersion ability, a lower VC was found to result from a lower PBL height and reduced horizontal winds, which indicated that the ability of the atmosphere to transport and diffuse pollutants was weakened. In terms of vertical dispersion ability, the aerosol radiative effect stabilized the lower atmosphere and weakened the vertical dispersion of pollutants, trapping the pollutants near the surface. Consequently, the PM2.5 concentration in the central and northwestern YRD increased by 6–18 μg m–3—no more than 15% of the average PM2.5 concentration in Phase 2.

(4) In Nanjing, the PM2.5 and PM10 concentrations increased below 950 hPa, with maxima of increase of 7 and 8 μg m–3, respectively, whereas they decreased between 950 and 800 hPa, with maxima of decrease of –3.5 and –4.5 μg m–3. However, the situation was the opposite for the variation of the O3 concentration, which decreased by up to 1.1 μg m–3 below 950 hPa and increased by up to 1.7 μg m–3 between 950 and 770 hPa. The aerosol radiative effect changed the vertical distribution of pollutants, and the influence varied among different kinds of pollutants.

This paper reveals that, in the heavy haze event studied, the aerosol radiative effect aggravated the level of pollution to some extent, but was not the determining factor for the formation of the haze. Rather, the stagnant meteorological conditions weakened the dispersion of pollutants and, together with the sustained emission of pollutants, resulted in the high pollutant concentration and the related heavy haze event. Nonetheless, our study demonstrates that, in air quality simulation and forecasting, we should still pay attention to the influence of aerosol radiative feedback.

Acknowledgments. The numerical calculations were carried out with the computing facilities at the High Performance Computing Center of Nanjing University. We also acknowledge the free use of MEIC data (http://www.meicmodel.org).

References