本研究以模型場規模兩段式AO程序處理含高濃度有機氮之光電廢水，主要針對硝化與脫硝功能提升之策略分別進行探討，並且與模型廠之操作參數及功能指標進行評估，同時結合分子生物方法探討光電廢水處理系統中微生物之族群變化。
在此模型場規模中缺氧脫硝槽體積為2.4 m3，好氧硝化槽為三槽串聯，各別反應體積各為2.7m3，以現場混合廢水作為進流基質(TKN/COD = 0.15)，進入缺氧脫硝槽進行異營性脫硝反應(COD降解以及硝酸氮之去除)後，再進入串聯式好氧硝化槽進行自營性硝化反應，其硝化槽中產生之硝酸氮再迴流至缺氧脫硝槽提供電子接受者以達到總氮之去除。
研究初期缺氧槽脫硝功能表現不彰，進流水中COD殘留至好氧槽，導致自營性硝化功能不顯著且無硝酸氮生成以提供脫硝槽去除COD之電子接受者。為克服此現象，於是提升缺氧脫硝槽功能為首要目標，其策略為額外添加硝酸鹽氮於缺氧槽中模擬好氧槽迴流水中所提供之硝酸鹽氮作為電子接收者，強化缺氧槽中異營脫硝菌活性，經兩個月強化馴養後缺氧槽單位微生物去除量可達0.142 kg COD/kg-VSS-day ，硝酸鹽氮亦可達100%轉換；在好氧硝化槽有機物體積負荷降低後仍無明顯硝化現象，於是重新植入具有硝化活性之好氧污泥後並以固定式擔體置入槽中截留微生物，增加反應槽之SRT作為硝化功能提升之策略，策略執行後隨即可發現硝化活性漸升，整體氨氮轉換率於一個月內達到100%，F(NH4+-N)r/M可以達0.051 kg NH4+-N/kg-VSS-day。
在此研究中亦針對不同碳源進行脫硝活性評估，在光電廢水處理系統中，醋酸、PI廢液皆為一良好之碳源選擇，其比脫硝速率分別為5.32 mg-N/gVSS-hr以及5.92 mg-N/gSS-hr ，丙酮經一段時間馴養亦可達到一良好之脫硝速率高達7.44 mg-N/gVSS-hr；在光電廢水處理系統中異營脫硝菌主要利用基質為MEA供獻之有機碳源，以DMSO以及TMAH作為脫硝碳源時期脫硝活性皆不佳。
以專一性引子配合尾端修飾限制片段長度多型性(Terminal Restriction Fragment Length Polymorphism, T-RFLP)監測光電廢水處理程序好氧硝化槽中氨氧化菌變化，發現系統中以Nitrosomonas europea 為主，期間植入一以Nitrosospira sp. 為主之好氧硝化污泥，於14天後隨即消失，可能因其適應能力較差，容易隨著水流而流失；在好氧硝化槽功能彰顯後各槽中懸浮污泥以及固定擔體上之生物膜中AOB菌相皆以Nitrosomonas europea 為主。
以16S rRNA cloning library建立缺氧脫硝槽脫硝活性最佳時期之微生物菌相，系統中約22%微生物菌相以Dechloromonas sp.為主，主要利用MEA代謝過程中形成之醋酸作為脫硝碳源，亦有12%之比例為硫氧化菌相關菌種，與DMSO代謝過程最中形成硫酸鹽類有關。

A pilot-scaled AO process treating TFT-LCD wastewater which contaminated with strong nitrogen was evaluated this study. The main point were focus on enhance strategies of anoxic denitrification and oxic nitrification, evaluation of operating parameters and functional indicators and microbial population dynamic with molecular analysis.
In this AO process pilot plan, the volume of anoxic denitrification reactor is 2.4 m3, and the volume of oxic nitrification reactor is 2.7 m3 which is one of the three series reactors. The influent is practical photonic wastewater which TKN/COD ratio is 0.15. In the AO process, nitrate and organic carbon provided anoxic denitrification reaction and organic nitrogen was degraded to ammonia. Ammonia oxidized to nitrate in the oxic nitrification reactors and nitrate was recirculated back to anoxic tank.
During the study, the anoxic denitrification was able to degrade COD efficienctly while adding nitrate in anoxic tank. The Fr/M ratio was 0.142 kg COD/kg-VSS-day after two month enchancement. In addition, the nitrification could convert ammonia to nitrate efficiently with carriers while COD volumetric loading rate was decreased in anoxic tank. The F(NH4+-N)r/M ratio was 0.051 kg NH4+-N/kg-VSS-day in run6.
In this study, the activity of denitrfication with different carbon source were assayed. In the photonic wastewater treatment, the acetic acid, the PI wastewater were better carbon sources The SDNR were 5.32 mg-N/gVSS-hr and 5.92 mg-N/gSS-hr in respectively. The acetone could be utilized as carbon source while incubation in months and the SDNR was 7.44 mg-N/gVSS-hr. In the study, MEA was the main organic carbon source in anoxic tank for denitrifing bacteria. However, TMAH and DMSO could not be degraded by denitrifier as carbon source.
The microbial diversity of ammonia oxidizingbacteria(AOB) was monitored using terminal restriction fragment length polymorphism(T-RFLP). Nitrosomonas europea was dominant AOB in oxic tank. Based on cloning-sequence analysis with the sample taken at day 192 in anoxic tank, Dechloromonas sp. and sulfur oxidation organism were 22% and 12%.

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