On June 5, 2008, the “Act on Special Cases Concerning the Simplification of Authorization and Permission Procedures for Industrial Complexes” (Act No. 9106) was enacted. When it was implemented in August 2008, many industrial complex development projects were established, and the number of industrial complexes growth rates of 3 6% during 2003 2007 rose to around 15% in 2008. With the increase in industrial complexes, the environmental impacts of individual projects were examined, but comprehensive regional reviews of environmental impacts were not undertaken. In this study, we determined changes in air quality by applying the industrial complex development plan that completed the consultation at the end of 2010 to assess the comprehensive regional environmental impacts and presented the adequacy review plan for future industrial development plans based on the study’s results. When considering these industrial complex development plans, emissions in North Jeolla and South Chungcheong Provinces and Daegu City have increased significantly. Air quality analyses showed that the 24 h mean SO2 concentration in Daegu increased by more than 50% in summer compared to air quality concentrations in summer. The 24 h mean PM10 and NO2 concentrations increased by approximately 12 and 30%, respectively, in North Jeolla Province in summer. Areas exceeding the air quality standard for 1 h mean O3 concentration increased by more than 3,500 km2. Based on the above analysis, changes in air quality should be anticipated through a comprehensive evaluation of long-term development plans. Furthermore, control of air quality in accordance with the development of future industrial complexes is possible.

The objective of this work is the air quality modeling according to the scenarios of emission on complex terrain. The prognostic meteorological fields and air quality field over complex areas of Seoul, Korea are generated by the PSU/NCAR mesoscale model (MM5) and the Third Generation Community Multi-scale Air Quality Modeling System (Models - 3/CMAQ), respectively. The emission source was driven from the Clean Air Policy Support System of the Korea National institute of Environmental Research (CAPSS), which is a 1 km x 1 km grid in South Korea during 2003. In comparison of air quality fields, the simulated averaged PM10, NO2, and O3 concentration on complex terrain in control case were decreased as compared with base case. Particularly PM10 revealed most substantial localized differences by (18 ～ 24 μg/m3). The reduction rate of PM10, NO2, and O3 is respectively 18.88, 13.34 and 4.17%.

It has been researched the relationship between deposition velocity and factors which could affect the deposition phenomena and deposition velocity also has been estimated for several land-use types. The typical deposition velocities are complex functions of surface types, atmospheric stabilities, friction velocities, air pollutants and so on. The canopy resistance is major contribution to the model's total resistance for O3. Canopy wetness is also an important factor to calculate deposition velocity. We considered the canopy wetness as canopy water content(CWC) in our Model. But, it is not easy to observe CWC over each land-use types. In this study, we use CWC observed by EMEFS(CANADA Environment Service, 1988) to examine the influence of CWC in estimation of O3 dry deposition velocity(Vd) in summertime. The value of O3 Vd range 0.2～0.7 cms-1 on dry surface and 0.01～0.35 cms-1 on wet surface in daytime.

The purpose of this study is to estimate wet deposition flux and to investigate wet deposition characteristics by using the ADOM model. Wet deposition flux of highly reactive SO2 is estimated by applying observed meteorological parameters and concentrations of chemical species to the ADOM model. Wet deposition is largely dependent on large scale precipitation and cloud thickness. Wet deposition flux of sulfate depends on SO2 oxidation in clouds. When large amount of SO2 is converted to sulfate, deposition flux of sulfate increases, but wet deposition flux of SO2 is small. On the whole, the pattern of sulfate wet deposition flux agrees with the typical pattern of sulfate wet deposition that is high in the summer(July) and low in the winter(January).

Land-use types should be included in air pollutant diffusion model because a complex mixture of various land-use patterns with computational grid can make errors in calculation of several parameters. However, the air pollutant diffusion model has generally been treated with a uniform component with land-use type in each mesh because of the complexity of the simulation. This study presents a numerical simulation of the horizontal distribution of O3 dry deposition velocity during summertime in Busan metropolitan city. The calculation of the meteorological field was conducted using the land cover data. Simulation has been performed by the following two scenarios : (1) one with current land cover data, and (2) the other with only land and sea for the surface characteristics. The results from each scenario reveals considerable differences on the meteorological fields and these differences can cause changes in the calculation values of O3 deposition velocity.

The aerodynamic resistance(Ra) to vertical transfer in the surface boundary layer can be formulated in terms of the friction velocity, height of observation, vertical heat flux and surface roughness. Unlike previous studies which focused on the role of Rc, present study perform additional tests using a variety of Ra formulae. Several Ra formulations available in the literature, suitable for unstable conditions, were tested for their influence on the dry deposition velocity. The canopy resistance(Rc) determines the shape of the diurnal pattern, while a small amplitude diurnal cycle in Vd was attributed to the aerodynamic resistance. The aerodynamic resistance is the major contributor to the formation of spikes in nighttime and Ra is relatively important at night because the canopy resistance is smaller. All formulations show similar diurnal cycle and yield good agreement with the observations. Although present Vd formulations are suitable for numerical air quality models, the research must continue for further improvements in resistance parametrizations.

A predictive modal is demonstrated for gas removal rates from the atmosphere by dry deposition. Typical deposition velocities are complex functions of surface types, atmospheric stabilities, friction velocities, air pollutants, and so on. In this paper we simulated the calculation of dry deposition velocities near the earth surfaces, simultaneously we estimated real dry deposition velocities using the previous simulation. The measurement taken over a deciduous forest by Padro et al.(1988) were used to verify this model. In the comparison of the value of deposition velocity between numerical computation and observation, there are partially overestimations and underestimations between them, but we can speak that they are in a good accordance.