本研究之目的係探討台灣南部都會區2座都市垃圾焚化廠周圍大氣中戴奧辛/呋喃：(1) 特徵及固氣態分配比率；(2) 乾/溼沉降通量與速率；(3) 在冬季及夏季之乾沉降變化；(4) 在乾季及濕季之濕沉降變化；及(5)與鄰近工業廢棄物焚化廠之比較。
研究結果顯示，在2009年7月到2010年6月期間，都市垃圾焚化廠周圍大氣中戴奧辛/呋喃之濃度為0.0348 - 0.106 pg I-TEQ/Nm3，低於工業廢棄物焚化爐之平均濃度0.150 pg I-TEQ/Nm3。
大氣中戴奧辛/呋喃在冬季之濃度相對高於夏季，估算大氣中戴奧辛/呋喃之總乾沉降通量介於0.0274 - 0.718 ng I-TEQ/m2-month，且冬季之沉降通量高於夏季。結果顯示大氣固體微粒之乾沉降速率，在採樣地區A每月介於 0.52 - 0.91 cm/s (平均0.63 cm/s) ，在採樣地區B每月介於0.48 - 0.73 cm/s (平均0.55 cm/s) ，相似於鄰近之工業廢棄物焚化廠周圍。
此外，前述兩採樣地區在研究期間之戴奧辛/呋喃乾沉降主要為粒狀相所貢獻，此結果顯示乾沉降主要機制為粒狀相沉降所掌控；另在大氣中戴奧辛/呋喃之濕沉降過程，結果顯示亦由粒狀相沉降所主導，尤其較高氯數之同化物可觀察到較大的數值；而大氣周遭的溫度和降水量在戴奧辛/呋喃之沉降變化上扮演重要的角色，可發現溫度和戴奧辛/呋喃之粒狀相存在呈現負相關，顯示戴奧辛/呋喃之清除在寒冷的天氣時有較高效率。
戴奧辛/呋喃之濕沉降通量在濕季時（6月~8月）顯著地高於乾季時（12月~2月），顯示濕沉降通量和月降雨之間呈正相關；此外，在採樣地區A及採樣地區B之戴奧辛/呋喃每年乾沉降加溼沉降總通量和分別為149 ng/m2-year (5.02 ng I-TEQ/m2-year) 及177 ng/m2-year (5.11 ng I-TEQ/m2-year) ，溼沉降貢獻量分別佔20.8 %（19.2 %）及23.2 %（21.8 %），顯示在戴奧辛/呋喃之沉降通量中乾沉降比濕沉降為更主要的支配因素。
另參考文獻岡山及仁武垃圾焚化廠周界大氣乾/溼沉降模擬結果顯示，其總乾/溼沉降通量分別為8.59及10.1 ng I-TEQ/m2 -year，溼沉降貢獻量分別佔42及34 %，同樣顯示乾沉降比溼沉降重要。
因大氣沉降被視為戴奧辛/呋喃轉移至食物鏈之主要途徑，它對人體暴露於戴奧辛/呋喃的衝擊是非常重要；上述研究結果亦可做為進一步研究台灣戴奧辛/呋喃大氣乾/溼沉降之寶貴資訊。

The characteristics of polychlorinated dibenzo-p-dioxins and dibenzofurans (PCDD/Fs) and the variation of the gas-particle partitioning of PCDD/Fs near two municipal solid waste incinerators (MSWIs) located in southern Taiwan were investigated. In order to better understand the mechanism of dry deposition, the atmospheric dry deposition flux and velocity of PCDD/Fs were calculated. It was found that the mean atmospheric PCDD/F concentrations (0.0348-0.106 pg I-TEQ/Nm3) were comparable to those detected in the vicinity of MSWIs in Taiwan, but significantly lower than those in a highly industrialized urban area (0.150 pg I-TEQ/Nm3) located in southern Taiwan. The relatively higher atmospheric PCDD/F concentrations was found in winter than in summer. The calculated total dry deposition flux of PCDD/Fs ranged from 0.0274-0.718 ng I-TEQ/m2-month, and the atmospheric deposition flux in winter tended to be higher than those in summer. The results also indicated that dry deposition velocities of atmospheric particles for each month ranged from 0.52-0.91 cm/s (mean = 0.63 cm/s) and 0.48-0.73 cm/s (mean = 0.55 cm/s) in sites A and B, respectively, which were similar to that for the ambient air near two MSWIs in Taiwan, but slightly higher than those in urban area of Korea. In addition, the dry deposition of PCDD/Fs was mainly contributed by particle-phase at both sampling areas during the estimated period. The above results demonstrated that the dominant mechanism of dry deposition was particle phase deposition.
The annual variations of wet deposition of polychlorinated dibenzo-p-dioxins and dibenzofurans (PCDD/Fs) in atmosphere were also measured at two sites (A and B). Results showed that particle scavenging dominates in the wet deposition processes for the removal of PCDD/Fs from the atmosphere, the highest value was observed at the highest chlorinated congener. The ambient temperature and the amount of precipitation played an important role in the variation of PCDD/F deposition fluxes. It was found that temperature was inversely associated with the existence of particulate PCDD/Fs, indicating PCDD/Fs are scavenged most efficiently in cold weather. PCDD/F wet deposition fluxes in rainy seasons (from June to August) were significantly higher than those in dry seasons (from December to February), revealing a positive relationship between wet deposition flux and monthly rainfall. Additionally, the annual total (dry + wet) deposition fluxes of PCDD/Fs were 149 ng/m2-year (5.02 ng I-TEQ/m2-year) and 177 ng/m2-year (5.11 ng I-TEQ/m2-year) for sites A and B, respectively, revealing that dry deposition was more dominant than the wet deposition for the atmospheric deposition of PCDD/Fs. Since atmospheric deposition is believed to be the main transfer pathway of PCDD/Fs into food chains, its impact on human exposure to PCDD/Fs is of great importance.

摘要 II
Abstract IV
致謝 VII
Table of Contents VIII
List of Tables X
List of Figure XII
1. INTRODUCTION 1
2. Literature review 5
2.1. Chemical properties of PCDD/Fs 6
2.2. Toxic equivalency factors for PCDD/Fs 8
2.3. Gas/particle partitioning 11
2.4. Dry deposition processes of PCDD/Fs 13
2.5. Wet deposition processes of PCDD/Fs 14
3. MATERIALS AND METHODS 19
3.1. PCDD/F sampling 19
3.2. Analyses of PCDD/Fs 21
3.3. Gas-particle partitioning 22
3.4. Atmospheric dry deposition of PCDD/Fs 23
3.5. Atmospheric wet deposition of PCDD/Fs 24
4. RESULTS AND DISCUSSION 27
4.1. Concentrations of PCDD/Fs in the ambient air 27
4.2. Gas-particle partitioning of PCDD/Fs 32
4.3. Dry deposition flux of PCDD/Fs 40
4.4. Dry deposition velocity of PCDD/Fs 45
4.5. Gas-particle concentration of PCDD/Fs 47
4.6. Scavenging ratio 48
4.7. Wet deposition flux of PCDD/Fs 55
4.8. Annual total deposition flux of PCDD/Fs 57
5. Conclusions and suggestions 64
5.1. Conclusions 64
5.2. Suggestions 65
References 66

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