戴奧辛/呋喃(PCDD/Fs)是具毒性的化學物質，會造成生物體的生物累積以及引起內分泌中斷。這項研究透過包括可燃實驗室固體廢棄物(LSW)，實驗室塑料廢棄物（LPW）和有機實驗室廢液（LLW）的焚化比較來描述實驗室廢棄物焚化過程，針對焚化爐煙道氣（SFG），底灰（BTA），第一急冷塔灰（FQA），第二急冷塔灰（SQA），和濾袋灰（BHA）進行採樣，並使用高解析氣相譜分析/高解析質譜儀（HRGC / HRMS）測定以及進行生物檢知，來瞭解其戴奧辛/呋喃（PCDD/F）的排放特徵。其中操作時SFG的PCDD/F濃度符合台灣標準，而LPW和LLW的氯含量大致與都市固體廢棄物（MSW）相當，其PCDD/F的分布類似於都市垃圾焚化爐。因LSW有非常高的氯含量（11.4％），其焚化過程整個排放因子為888 ng I-TEQ /噸廢物，這是10倍以上都市生活垃圾焚化的排放量。在此實驗室廢棄物焚化爐其PCDD / F排放重量比主要集中在BTA（31.6％）和飛灰（63.1％），其中飛灰的PCDD/F含量較垃圾焚化爐的飛灰高出十倍。無論HRGC / HRMS分析和生物測定結果，LW在焚化過程中有類似的PCDD / F排放特性。
實驗室廢棄物為來自實驗、測試或分析過程中排出，含有具有高發熱值和高氯含量（> 9％）、各種有毒的化(混)合物。通常高濃度PCDD / F的排放可能來自於有高氯含量的燃燒，燃燒不完全，和所謂“記憶效應”所造成。其中冷啟爐階段因為時間短，其PCDD/F的污染容易被忽略，但與一個垃圾焚化爐在連續穩定運行時期相比，其PCDD/F排放對人類健康和環境的負面影響卻不容忽視。這項研究針對實驗室廢棄物焚化爐進行調查，該焚化爐為每次運行10天，每年啟爐15至20次的小型焚化爐。在冷啟爐期間(啟爐60.5小時內)，收集煙道氣十一個PCDD/F的樣品。主燃燒室的氣體的溫度高於850℃時開始採樣，測試時僅使用柴油且無廢棄物進料的限制下，並將主燃燒室溫度維持 850-900℃之間。結果發現對於開始取樣的第1.5-7.5小時，煙囪氣中的PCDD / F濃度高達0.656-1.15 ng I-TEQ / Nm3。隨後，在第10.5-35.5和54.5-60.5小時區間，分別減少到0.159-0.459和0.218-0.254 ng I-TEQ / Nm3。另依據主成分分析（PCA）獲得H(六，七和八氯數) /L(四和五氯)值，結果顯示32小時前具較低的H/L比值（0.81），說明此時是低氯化PCDD/F同源物為主，而於第32小時之後高氯化PCDD / F同源物有較高的質量濃度(H/L比值昇至2.38)。
PCDD/F的排放具有獨特模式，可作為戴奧辛/呋喃的指紋，研究大多數集中在各類焚化爐或不同的熱處理行為的排放特性進行比對，本計畫特進行同一焚化爐(同一焚化爐)焚化不同類的廢棄物進行排放源特徵的探討。在這研究中，利用PCDF/PCDD比、總排放因子、輸入/輸出比（O / I比率）、H / L比，描述觀察到空氣污染物控制裝置（APCDs）的設置及冷卻方式將影響PCDD/F的排放特性，進一步利用區別分析（DA）的效果來陳述PCDD/F排放特性並建立污染源的預測參數，來預測污染物來源。
在本研究使用這儀器分析及生物檢知兩種方法，兩值之間的線性回歸顯示出良好的關係（R2> 0.84），未來利用Ad-DR生物測定用於確定非生物性毒性的PCDD / F毒性當量濃度檢測有前途且快速方法。另一方面，在冷啟爐時的PCDD/F 排放是源於記憶效應和熱脫附所造成。因此，強烈建議起爐階段應於袋濾式集塵器前噴注更多的活性碳量，來減少來自廢棄物焚化爐的煙道氣的PCDD/F排放。

Polychlorinated dibenzo-p-dioxins and dibenzofurans (PCDD/Fs) are extremely toxic chemicals that can bio-accumulate in the biotic materials, cause endocrines disruption. This study describes PCDD/F behavior during the incineration of laboratory waste, including combustible laboratory solid waste (LSW), laboratory plastic waste (LPW), and organic laboratory liquid waste (LLW). Stack flue gas (SFG), input materials, bottom ash (BTA), first quenching tower ash (FQA), secondary quenching tower ash (SQA), and baghouse ash (BHA) were sampled and analyzed using high-resolution gas chromatography/high-resolution mass spectrometry (HRGC/HRMS) assay and bioassay. The PCDD/F concentration of SFG met the standard in Taiwan. The Cl levels of LPW and LLW were roughly equivalent to that of municipal solid waste (MSW). Therefore, the SFG concentration, content of fly ash, and distribution behavior of PCDD/Fs are reasonably similar to those of MSW incinerators. The LSW had an extremely high Cl level (11.4%). The emission factor of the whole incineration system was 888 μg I-TEQ/ton-waste, which is 10-fold higher than that of MSW. The PCDD/F was mainly in BTA (31.6 wt.%) and fly ash (63.1 wt.%), resulting in higher PCDD/F level of ashes compared with that of MSW ashes.
Laboratory wastes are discharged from experimental, testing, or analysis processes, and contain various toxic chemical compounds with a high heating-value and a high chlorine content (> 9%). Elevated PCDD/F emissions are caused by combustion of waste with high chlorine contents, incomplete combustion, and so called "memory effects". Even though the duration of cold start-up is short compared with the hours of continuous steady operation in a waste incinerator, its negative effects with regard to PCDD/F emissions on both human health and the environment cannot be neglected. A full-scale laboratory-waste incinerator which is operated for 10 days in each run and has 15 to 20 runs annually was investigated in this study. Eleven PCDD/F samples of stack flue gas were collected during the cold start-up periods (for 60.5 hrs). The gas temperature of the primary combustion chamber was above 850°C, and was maintained at between 850 and 900°C by injecting diesel fuel without waste feed. For first 1.5–7.5 hours, the PCDD/F concentration in the stack flue gas was as high as 0.656–1.15 ng I-TEQ/Nm3. Afterward, during hours 10.5–35.5 and 54.5–60.5, this reduced to 0.159–0.459 and 0.218–0.254 ng I-TEQ/Nm3, respectively. Based on principal component analysis (PCA) and the H/L ratio, the results revealed a lower H/L ratio (0.81) before hour 32, indicating that less chlorinated PCDD/F homologues (tetra- and penta-) dominated, while after hour 32 more chlorinated PCDD/F homologues (hexa-, hepta- and octa-) had a higher concentration and the H/L ratio rises to 2.38. These results indicate that the PCDD/F emissions during cold start-up were caused by memory effects and thermal desorption.
Most literatures focused on comparison of different thermal processes or emission characteristics in the various types of incinerator, but this study conducts some surveys with various types of wastes feeding in the same incinerator. The whole system emission factor including the PCDD/F emission of stack flue gas, bottom ash, fly ash, wastewater of wet scrubber were distinguished. PCDF/PCDD ratio, emission factor, output/input ratios (O/I ratios), H(hexa-, hepta- and octa-)/L(tetra- and penta-) ratio High-Chlorinated congeners/Low-Chlorinated congeners were observed to demonstrate the emission characteristic of PCDD/Fs. The unique patterns of PCDD/F can be used as PCDD/F “fingerprints”, but limited studies have evaluated significant PCDD/F fingerprint predictors. More available emission characteristics are needed from different types of sources, to discriminate the category of emission sources to which the individual belongs to.
Both HRGC/HRMS analysis and bioassay results show similar PCDD/F emission characteristics during the incineration of LW. In addition, the linear regression between the values acquired using these two methods show a good relation (R2 >0.84), indicating that Ad-DR bioassay is a promising fast-screen method for determining PCDD/F levels. Additionally, in order to reduce the PCDD/F emissions from the stack flue gas of waste incinerators, is highly recommended that a higher amount of activated carbon injection is used in front of the bag filters.

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