環保專案成果報告查詢系統

專案計畫編號	EPA-112-XB06
經費年度	112
計畫經費	2,000 千元
預算科目	補助及獎勵回收清除處理暨再生利用
專案開始日期	2023/02/18
專案結束日期	2023/11/30
專案主持人	郭益銘
主辦單位	循環署回收基金管理會
承辦人	趙國芬
執行單位	中華醫事科技大學／環境與安全衛生工程系
專案分類	資源循環、廢棄物管理
中文關鍵字	衍生鉛渣、重金屬、紅磚
英文關鍵字	Lead-containing furnace slag, Heavy metals, Bricks
協同主持人
共同主持人
計畫聯絡人	黃宇婷
計畫聯絡電話	06-2674567#860
計畫聯絡信箱	kuolabworks@gmail.com

中文摘要	環保署已於民國78年正式公告廢鉛酸蓄電池為應回收廢棄物，近年鉛蓄電池回收每年達到5~7萬公噸，目前台灣的對於回收之廢鉛蓄電池多使用火法冶煉程序進行回收金屬鉛，然而與一般金屬二級冶煉廠會面臨到相同之問題，最終無法繼續精煉之爐渣去化問題，且鉛為公告有害事業廢棄物標準之一，因此處理方式多半是固化後進行掩埋，近年來隨著掩埋場逐漸達到飽和，處理費用也隨之提高。本計畫探討衍生鉛渣替代部分紅磚原料之可行性，於實驗室所進行之毒性溶出實驗結果觀之，鉛渣中Pb溶出值高達417 mg/L，各試程紅磚試體之Pb溶出值已降至僅約0.06~0.35 mg/L；而於實廠所製造之紅磚，其Pb之溶出值則為0.13 mg/L，已符合再生料規範之之0.3 mg/L，顯示透過紅磚燒結後，Pb元素已被黏土包匣固化於鋁矽晶格之中，其溶出之風險相對較低。在紅磚抗壓強度及吸水率試驗中，添加量1%、2.5%、5%和10%中，吸水率與抗壓強度均有達到第三種磚之規範，於實廠磚部分，其抗壓強度亦有達到第三種磚之規範，而吸水率雖高於規範，但由於在實驗室製作磚坯採人工方式製作，若使用專業製磚設備應可達到規範要求，因此於實驗室試程中以添加量1%為最適化配比。 Pb燒失量與揮發量推估中，Pb燒失量主要散失階段為於800℃~850℃區間，後續隨溫度與時間提升，發現其燒失變化量不大。在Pb揮發量推估計算後，其揮發比例為19.83%，顯示添加Pb含量較高之物質仍會影響排放尾氣，因此在燒製摻有鉛渣之紅磚應注意其摻配量，建議若欲提升處理量能應考慮增加後端污染防制設備，提升處理量能。
中文關鍵字	衍生鉛渣、重金屬、紅磚

中文摘要

環保署已於民國78年正式公告廢鉛酸蓄電池為應回收廢棄物，近年鉛蓄電池回收每年達到5~7萬公噸，目前台灣的對於回收之廢鉛蓄電池多使用火法冶煉程序進行回收金屬鉛，然而與一般金屬二級冶煉廠會面臨到相同之問題，最終無法繼續精煉之爐渣去化問題，且鉛為公告有害事業廢棄物標準之一，因此處理方式多半是固化後進行掩埋，近年來隨著掩埋場逐漸達到飽和，處理費用也隨之提高。本計畫探討衍生鉛渣替代部分紅磚原料之可行性，於實驗室所進行之毒性溶出實驗結果觀之，鉛渣中Pb溶出值高達417 mg/L，各試程紅磚試體之Pb溶出值已降至僅約0.06~0.35 mg/L；而於實廠所製造之紅磚，其Pb之溶出值則為0.13 mg/L，已符合再生料規範之之0.3 mg/L，顯示透過紅磚燒結後，Pb元素已被黏土包匣固化於鋁矽晶格之中，其溶出之風險相對較低。在紅磚抗壓強度及吸水率試驗中，添加量1%、2.5%、5%和10%中，吸水率與抗壓強度均有達到第三種磚之規範，於實廠磚部分，其抗壓強度亦有達到第三種磚之規範，而吸水率雖高於規範，但由於在實驗室製作磚坯採人工方式製作，若使用專業製磚設備應可達到規範要求，因此於實驗室試程中以添加量1%為最適化配比。 Pb燒失量與揮發量推估中，Pb燒失量主要散失階段為於800℃~850℃區間，後續隨溫度與時間提升，發現其燒失變化量不大。在Pb揮發量推估計算後，其揮發比例為19.83%，顯示添加Pb含量較高之物質仍會影響排放尾氣，因此在燒製摻有鉛渣之紅磚應注意其摻配量，建議若欲提升處理量能應考慮增加後端污染防制設備，提升處理量能。

中文關鍵字

衍生鉛渣、重金屬、紅磚

類型	檔名	檔案大小	說明	最新版公開日期
期末報告	EPA-112-XB06-(期末報告)「回收廢鉛蓄電池衍生鉛渣轉質環保紅磚之技術研究」-(定稿).pdf	58MB		2024/2/9 上午 12:00:00

摘要	The Environmental Protection Administration officially designated waste lead-acid batteries as recyclable waste in the year 1989. In recent years, the annual collection of lead batteries in Taiwan has reached 50,000 to 70,000 metric tons. Currently, the common method for recycling waste lead-acid batteries in Taiwan involves the pyrometallurgical process to recover lead metal. However, similar to general secondary metal smelters, the issue of final disposal of the resulting furnace slag presents a challenge. Furthermore, lead is classified as one of the hazardous industrial waste materials, leading to the predominant disposal method of solidification followed by landfilling. In recent years, as landfills gradually reach saturation, the associated disposal costs have been on the rise. This project explores the feasibility of using derived lead slag as a substitute for some of the raw materials in red brick manufacturing. Observing the results of toxicity leaching experiments conducted in the laboratory, the Pb leaching value in lead slag reaches as high as 417 mg/L. In contrast, the Pb leaching values for various red brick specimens range from only about 0.06 to 0.35 mg/L. For red bricks manufactured in the factory, the Pb leaching value is 0.13 mg/L, meeting the recycling material standard of 0.3 mg/L. This indicates that through the sintering process of red bricks, Pb elements have been solidified within the clay matrix of the aluminum-silicon crystal lattice, resulting in a relatively lower risk of leaching. In the compressive strength and water absorption tests for red bricks with addition levels of 1%, 2.5%, 5%, and 10%, both water absorption and compressive strength met the specifications for the third category of bricks. In the case of factory-produced bricks, compressive strength also met the third-category specifications, although water absorption was slightly higher than the standard. This difference is attributed to manual brick preparation in the laboratory. However, it is anticipated that using professional brick-making equipment in a factory setting would enable compliance with the standard requirements. Therefore, based on the laboratory trial results, the optimal ratio for the addition level was determined to be 1%. In the estimation of Pb loss and volatilization, the primary loss stage for Pb occurs in the temperature range of 800°C to 850°C. Subsequent increases in temperature and time show minimal changes in the loss variation. After calculating the estimated Pb volatilization, the volatile proportion is found to be 19.83%, indicating that materials with higher Pb content still impact exhaust emissions. Therefore, when producing red bricks containing lead slag, attention should be paid to the blending ratio. It is recommended that, if there is a desire to enhance processing capacity, consideration should be given to increasing pollution control measures at the backend to improve overall processing capabilities.
英文關鍵字	Lead-containing furnace slag, Heavy metals, Bricks

摘要

The Environmental Protection Administration officially designated waste lead-acid batteries as recyclable waste in the year 1989. In recent years, the annual collection of lead batteries in Taiwan has reached 50,000 to 70,000 metric tons. Currently, the common method for recycling waste lead-acid batteries in Taiwan involves the pyrometallurgical process to recover lead metal. However, similar to general secondary metal smelters, the issue of final disposal of the resulting furnace slag presents a challenge. Furthermore, lead is classified as one of the hazardous industrial waste materials, leading to the predominant disposal method of solidification followed by landfilling. In recent years, as landfills gradually reach saturation, the associated disposal costs have been on the rise. This project explores the feasibility of using derived lead slag as a substitute for some of the raw materials in red brick manufacturing. Observing the results of toxicity leaching experiments conducted in the laboratory, the Pb leaching value in lead slag reaches as high as 417 mg/L. In contrast, the Pb leaching values for various red brick specimens range from only about 0.06 to 0.35 mg/L. For red bricks manufactured in the factory, the Pb leaching value is 0.13 mg/L, meeting the recycling material standard of 0.3 mg/L. This indicates that through the sintering process of red bricks, Pb elements have been solidified within the clay matrix of the aluminum-silicon crystal lattice, resulting in a relatively lower risk of leaching. In the compressive strength and water absorption tests for red bricks with addition levels of 1%, 2.5%, 5%, and 10%, both water absorption and compressive strength met the specifications for the third category of bricks. In the case of factory-produced bricks, compressive strength also met the third-category specifications, although water absorption was slightly higher than the standard. This difference is attributed to manual brick preparation in the laboratory. However, it is anticipated that using professional brick-making equipment in a factory setting would enable compliance with the standard requirements. Therefore, based on the laboratory trial results, the optimal ratio for the addition level was determined to be 1%. In the estimation of Pb loss and volatilization, the primary loss stage for Pb occurs in the temperature range of 800°C to 850°C. Subsequent increases in temperature and time show minimal changes in the loss variation. After calculating the estimated Pb volatilization, the volatile proportion is found to be 19.83%, indicating that materials with higher Pb content still impact exhaust emissions. Therefore, when producing red bricks containing lead slag, attention should be paid to the blending ratio. It is recommended that, if there is a desire to enhance processing capacity, consideration should be given to increasing pollution control measures at the backend to improve overall processing capabilities.

英文關鍵字

Lead-containing furnace slag, Heavy metals, Bricks