李冬1,赵世勋1,王俊安2,关宏伟1,朱金凤1,张杰1,3
(1.水质科学与水环境恢复工程北京市重点实验室(北京工业大学),北京100124;2.北京桑德环保集团技术研发中心,北京101102;3.城市水资源与水环境国家重点实验室(哈尔滨工业大学),哈尔滨150090)
摘要:
为研究污水处理厂厌氧氨氧化(Anammox)工艺可行性,在实际生活污水处理厂中进行厌氧氨氧化工艺的小试实验.向污水厂A/O除磷工艺出水中投加亚硝酸盐作为基质,启动厌氧氨氧化滤柱.反应器启动成功后,进水改为A/O除磷和亚硝化工艺处理后的生活污水,观察厌氧氨氧化工艺实际工程应用的效果.结果表明,第106~144天,进水温度为15~20 ℃,最大出水氨氮和总氮质量浓度为4.1和13.4 mg/L,出水氮素满足国家一级A排放标准;第168~204天,反应器运行进入冬季,进水温度为12~15 ℃,采用延长水力停留时间的方法实现污水处理达标;第222~240天时,水温降低到10~12 ℃,在进水投加125 mg/L碳酸氢钠,总氮去除负荷提高了40%,最大出水氨氮和总氮质量浓度为1.4和13.6 mg/L,冬季出水氮素达标.在整个过程中滤柱生物膜厚度持续增加,最终达113 μm,单位MLSS污泥厌氧氨氧化负荷大于5 kg/(kg·d),厌氧氨氧化工艺在市政污水处理厂高效稳定运行.
关键词: 生活污水 厌氧氨氧化 低温 滤柱 生物膜
DOI:10.11918/j.issn.0367-6234.201704073
分类号:X523
文献标识码:A
基金项目:国家自然科学基金优秀青年科学基金(51222807)
Operation of lab-scaleanammox process with effluent from A/O process which operated in wastewater treatment plant as substrate
LI Dong1,ZHAO Shixun1,WANG Junan2,GUAN Hongwei1,ZHU Jinfeng1,ZHANG Jie1,3
(1.Key Laboratory of Beijing for Water Quality Science and Water Environment Recovery Engineering(Beijing University of Technology),Beijing 100124, China; 2.Technology Research and Development Center, Beijing Sander Environmental Group, Beijing 101102, China;3.State Key Laboratory of Urban Water Resource and Environment (Harbin Institute of Technology), Harbin 150090, China)
Abstract:
In order to study the feasibility of anaerobic ammonia oxidation(Anammox) process in Waste Water Treatment Plant(WWTP), lab-scale Anammox reactor was employed in municipal WWTP. NaNO2 was added into the sewage effluent treated by A/O process in WWTP to serve as substance to start up Anammox filter reactor. In order to investigate the performance of Anammox process in engineering application, sewage effluent treated by A/O and nitrification process was served as inflow after the successful start-up of reactor. From the 106th to the 144th day, the maximal ammonia and total nitrogen concentrations in effluent were 4.1 and 13.4 mg/L with water temperature vary from 15 to 20 ℃ and the nitrogen concentration in effluent fitted the national 1A discharge standard of pollutants for municipal wastewater treatment plant. From the 168th to the 204th day, the reactor was running in the winter. When water temperature varied from 12 to 15 ℃, nitrogen concentration in effluent fitted the standard with the strategy of prolonging HRT. From the 222th to the 240th day, when the water temperature reduced to 10-12 ℃, NaHCO3 was added in inflow at a concentration of 125 mg/L. Nitrogen removal rate increasd 40 percents and the ammonia and total nitrogen in effluent was 1.4 and 13.6 mg/L. Nitrogen concentration in effluent reached the national 1A discharge standard of pollutants for municipal wastewater treatment plant in winter. The thickness of biomembrane increased continuely in the whole process of filter column and finally reached 113 μm. Ammonia anaerobic oxidation loading rate was greater than 5 kg/(kgMLSS·d) and Anammox process operated efficiently and stably.
Key words: sewage anammox low temperature filter biomembrane
李冬, 赵世勋, 王俊安, 关宏伟, 朱金凤, 张杰. 污水厂A/O除磷出水为基质的Anammox小试研究[J]. 哈尔滨工业大学学报, 2018, 50(8): 8-13. DOI: 10.11918/j.issn.0367-6234.201704073.
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LI Dong, ZHAO Shixun, WANG Junan, GUAN Hongwei, ZHU Jinfeng, ZHANG Jie. Operation of lab-scaleanammox process with effluent from A/O process which operated in wastewater treatment plant as substrate[J]. Journal of Harbin Institute of Technology, 2018, 50(8): 8-13. DOI: 10.11918/j.issn.0367-6234.201704073.
![复制到剪切板](http://hit.alljournals.cn/html/hitxb_cn/2018/8/images/copy.gif)
基金项目 国家自然科学基金优秀青年科学基金(51222807) 作者简介 李冬(1976—),女,教授,博士生导师;
张杰(1938—),男,博士生导师,中国工程院院士 通信作者 李冬, lidong2006@bjut.edu.cn 文章历史 收稿日期: 2017-04-15
Contents -->Abstract Full text Figures/Tables PDF
污水厂A/O除磷出水为基质的Anammox小试研究
李冬1
![通讯作者](http://hit.alljournals.cn/html/hitxb_cn/2018/8/images/REcor.gif)
![lidong2006@bjut.edu.cn](http://hit.alljournals.cn/html/hitxb_cn/2018/8/images/REemail.gif)
1. 水质科学与水环境恢复工程北京市重点实验室(北京工业大学),北京100124;
2. 北京桑德环保集团技术研发中心,北京101102;
3. 城市水资源与水环境国家重点实验室(哈尔滨工业大学),哈尔滨150090
收稿日期: 2017-04-15
基金项目: 国家自然科学基金优秀青年科学基金(51222807)
作者简介: 李冬(1976—),女,教授,博士生导师;
张杰(1938—),男,博士生导师,中国工程院院士
通信作者: 李冬, lidong2006@bjut.edu.cn
摘要: 为研究污水处理厂厌氧氨氧化(Anammox)工艺可行性,在实际生活污水处理厂中进行厌氧氨氧化工艺的小试实验.向污水厂A/O除磷工艺出水中投加亚硝酸盐作为基质,启动厌氧氨氧化滤柱.反应器启动成功后,进水改为A/O除磷和亚硝化工艺处理后的生活污水,观察厌氧氨氧化工艺实际工程应用的效果.结果表明,第106~144天,进水温度为15~20 ℃,最大出水氨氮和总氮质量浓度为4.1和13.4 mg/L,出水氮素满足国家一级A排放标准;第168~204天,反应器运行进入冬季,进水温度为12~15 ℃,采用延长水力停留时间的方法实现污水处理达标;第222~240天时,水温降低到10~12 ℃,在进水投加125 mg/L碳酸氢钠,总氮去除负荷提高了40%,最大出水氨氮和总氮质量浓度为1.4和13.6 mg/L,冬季出水氮素达标.在整个过程中滤柱生物膜厚度持续增加,最终达113 μm,单位MLSS污泥厌氧氨氧化负荷大于5 kg/(kg·d),厌氧氨氧化工艺在市政污水处理厂高效稳定运行.
关键词: 生活污水 厌氧氨氧化 低温 滤柱 生物膜
Operation of lab-scaleanammox process with effluent from A/O process which operated in wastewater treatment plant as substrate
LI Dong1
![Corresponding author](http://hit.alljournals.cn/html/hitxb_cn/2018/8/images/REcor.gif)
![lidong2006@bjut.edu.cn](http://hit.alljournals.cn/html/hitxb_cn/2018/8/images/REemail.gif)
1. Key Laboratory of Beijing for Water Quality Science and Water Environment Recovery Engineering(Beijing University of Technology), Beijing 100124, China;
2. Technology Research and Development Center, Beijing Sander Environmental Group, Beijing 101102, China;
3. State Key Laboratory of Urban Water Resource and Environment (Harbin Institute of Technology), Harbin 150090, China
Abstract: In order to study the feasibility of anaerobic ammonia oxidation(Anammox) process in Waste Water Treatment Plant(WWTP), lab-scale Anammox reactor was employed in municipal WWTP. NaNO2 was added into the sewage effluent treated by A/O process in WWTP to serve as substance to start up Anammox filter reactor. In order to investigate the performance of Anammox process in engineering application, sewage effluent treated by A/O and nitrification process was served as inflow after the successful start-up of reactor. From the 106th to the 144th day, the maximal ammonia and total nitrogen concentrations in effluent were 4.1 and 13.4 mg/L with water temperature vary from 15 to 20 ℃ and the nitrogen concentration in effluent fitted the national 1A discharge standard of pollutants for municipal wastewater treatment plant. From the 168th to the 204th day, the reactor was running in the winter. When water temperature varied from 12 to 15 ℃, nitrogen concentration in effluent fitted the standard with the strategy of prolonging HRT. From the 222th to the 240th day, when the water temperature reduced to 10-12 ℃, NaHCO3 was added in inflow at a concentration of 125 mg/L. Nitrogen removal rate increasd 40 percents and the ammonia and total nitrogen in effluent was 1.4 and 13.6 mg/L. Nitrogen concentration in effluent reached the national 1A discharge standard of pollutants for municipal wastewater treatment plant in winter. The thickness of biomembrane increased continuely in the whole process of filter column and finally reached 113 μm. Ammonia anaerobic oxidation loading rate was greater than 5 kg/(kgMLSS·d) and Anammox process operated efficiently and stably.
Key words: sewage anammox low temperature filter biomembrane
相比传统脱氮工艺,厌氧氨氧化工艺因脱氮途径短、节省了62.5%曝气量、无需外加碳源、温室气体排出少以及几乎不产生剩余污泥[1],成为了理想的污水脱氮工艺[2].厌氧氨氧化工艺的研究主要停留在高温、高氨氮的配水处理[3-4],而实际工程应用的研究较少,因此,市政污水处理厂厌氧氨氧化研究意义重大.厌氧氨氧化工艺适合处理高温、高氨氮污水,城市生活污水氨氮质量浓度为35~55 mg/L,温度为10~20 ℃,是典型的低温低氨氮水质,因此,将厌氧氨氧化工艺应用于市政污水处理厂困难重重[5].
本实验基于A/O除磷、亚硝化和厌氧氨氧化的污水再生全流程,在污水处理厂室外进行小试.在污水厂A/O除磷工艺出水中投加亚氮作为基质,常温条件下启动厌氧氨氧化滤柱.反应器启动成功后,将进水改为亚硝化工艺出水,研究厌氧氨氧化工艺在市政污水处理厂的运行效果,通过长期常温驯化和投加无机碳提高了低温厌氧氨氧化工艺的处理效果.
1 实验 1.1 实验装置实验采用上向流生物滤柱(图 1).反应器由有机玻璃制成,内径8 cm,承托层高5 cm,滤料高80 cm,有效体积5 L.滤柱内部装填直径5~10 mm的火山岩填料,底部设曝气装置以应对可能出现的滤柱堵塞.整个反应器外部用黑色保温棉缠绕以避光和保温.
Figure 1
![点击查看原图](http://hit.alljournals.cn/html/hitxb_cn/2018/8/PIC/hebgydxxb-50-8-8-1.jpg)
1.2 接种污泥和实验水质反应器启动时接种1 L厌氧氨氧化絮状污泥,污泥质量浓度为2 100 mg/L.厌氧氨氧化絮状污泥来自稳定运行的厌氧氨氧化SBR反应器,SBR反应器总氮去除率稳定在85%左右,总氮去除负荷为0.5 kg/(m3·d).
向污水处理厂A/O除磷工艺出水中投加50 mg/L NO2--N作为基质,启动厌氧氨氧化生物滤柱,水质如表 1所示.反应器启动成功后,进水改为经A/O除磷和亚硝化工艺处理后的实际生活污水,具体水质如表 2所示.
表 1
![点击查看表格内容](http://hit.alljournals.cn/html/hitxb_cn/2018/8/images/table-icon.gif)
(mg·L-1) ρ(NO2--N)/
(mg·L-1) ρ(NO3--N)/
(mg·L-1) SS/
(mg·L-1) COD/
(mg·L-1) pH TP/
(mg·L-1) t/℃
结果 35~60 40~55 < 2 < 20 20~50 7.3~7.9 < 1.5 14~20
表 1 A/O除磷出水水质 Table 1 Characteristics of the effluent from A/O process
表 2
![点击查看表格内容](http://hit.alljournals.cn/html/hitxb_cn/2018/8/images/table-icon.gif)
(mg·L-1) ρ(NO2--N)/
(mg·L-1) ρ(NO3--N)/
(mg·L-1) SS/
(mg·L-1) BOD/
(mg·L-1) pH TP/
(mg·L-1) t/℃
结果 15~22 16~24 4~8 < 20 < 30 7.0~7.6 < 1.5 14~20
表 2 亚硝化出水水质 Table 2 Characteristics of the effluent fromnitrification process
1.3 实验方法反应器各阶段运行参数如表 3所示.S1和S2阶段为反应器启动阶段,基质为投加亚硝酸盐后的A/O除磷出水,S1和S2阶段水力停留时间分别为3.5和1.75 h.S3、S4和S5阶段为稳定运行阶段,进水为经A/O除磷及亚硝化工艺处理的城市生活污水,S5阶段的基质中额外投加125 mg/L的NaHCO3.
表 3
![点击查看表格内容](http://hit.alljournals.cn/html/hitxb_cn/2018/8/images/table-icon.gif)
(mg·L-1) HRT/
h 季节 t/
℃
S1 1~72 d — 3.5 春、初夏 15~19
S2 73~105 d — 1.75 夏 15~21
S3 106~167 d — 1.75 秋 12~20
S4 168~217 d — 5 冬 10~15
S5 218~240 d 125 5 冬 10~12
表 3 各阶段反应器参数变化 Table 3 Parameter variations of each stage
1.4 检测方法水样分析中NH4+-N测定采用纳氏试剂光度法,NO2--N采用N-(1-萘基)乙二胺光度法,NO3--N采用紫外分光光度法,COD采用快速测定仪,DO、pH和水温通过WTW便携测定仪测定,IC采用TOC测定仪测定,其余水质指标的分析方法均采用国标方法.滤料表面生物膜厚度通过电子显微镜精确测量[6].
反应速率的测定:从反应器取出滤料,刮下生物膜解离并在烧杯中测定反应速率.烧杯设置机械搅拌,测定厌氧氨氧化反应速率和反硝化反应速率.测定厌氧氨氧化反应速率时,基质氨氮和亚氮质量浓度为50 mg/L,调节碱度使碱度与氨氮之比为10,温度控制在25 ℃,pH稳定在7.0~8.0,DO维持0.3 mg/L以下.测定反硝化反应速率时,以150 mg/L甲醇作为碳源,硝氮质量浓度为50 mg/L,温度控制在25 ℃,pH稳定在7~7.8,DO维持0.3 mg/L以下.
2 结果与讨论 2.1 反应器的启动污水处理厂厌氧氨氧化工艺在春季进行启动,水温为15~19 ℃.亚硝化工艺出水中氨氮和亚氮质量浓度为20 mg/L左右,而投加亚硝酸盐后的A/O除磷出水中氨氮和亚氮质量浓度为45 mg/L左右,高质量浓度的基质有利于加速反应器的启动.为了缩短反应器的启动时间,在秋季之前完成小试的启动,基质采用投加亚硝酸盐后的A/O除磷出水.反应器进出水氮素变化如图 2所示,氮素去除率如图 3所示.
Figure 2
![点击查看原图](http://hit.alljournals.cn/html/hitxb_cn/2018/8/PIC/hebgydxxb-50-8-8-2.jpg)
Figure 3
![点击查看原图](http://hit.alljournals.cn/html/hitxb_cn/2018/8/PIC/hebgydxxb-50-8-8-3.jpg)
为了宏观地研究反应器性能,引入厌氧氨氧化生化反应方程式[7]
$\begin{align} &\text{NH}_{4}^{+}\text{+1}\text{.32NO}_{2}^{-}\text{+0}\text{.13}{{\text{H}}^{\text{+}}}\text{+0}\text{.066HCO}_{3}^{-}\to \\ &\text{1}\text{.02}{{\text{N}}_{\text{2}}}\text{+0}\text{.26NO}_{3}^{-}\text{+0}\text{.066C}{{\text{H}}_{\text{2}}}{{\text{O}}_{\text{2}\text{.5}}}{{\text{N}}_{\text{0}\text{.15}}}\text{+2}\text{.03}{{\text{H}}_{\text{2}}}\text{O}\text{.} \\ \end{align}$ (1)
从反应式上可以得出,厌氧氨氧化菌按1.32:1的比例消耗亚氮和氨氮基质,最终生成氮气和少量硝氮.总氮去除量和硝氮增量之比为8,该值称为特征比.同时,亚氮氨氮消耗比和特征比受反硝化菌活性的影响,反硝化菌活性较高,亚氮氨氮消耗比和特征比均会上升.反应器亚氮氨氮消耗比和特征比如图 4所示.
Figure 4
![点击查看原图](http://hit.alljournals.cn/html/hitxb_cn/2018/8/PIC/hebgydxxb-50-8-8-4.jpg)
S1阶段滤柱氨氮、亚氮的去除率先下降后上升.滤柱启动第1天有着较高的氮素去除率,而特征比和亚氮氨氮消耗比不满足厌氧氨氧化反应方程式,氮损可能来源于火山岩填料对基质的吸附.随着反应器的继续运行,出水氮素质量浓度不断降低.第72天时,总氮去除率连续10 d大于75%,总氮去除负荷在0.5 kg/(m3·d)左右,反应器有很好的氮素去除效果.同时,特征比在7~10,亚氮氨氮消耗比稳定在1.15~1.3,符合厌氧氨氧化工艺的氮素去除比例,表明厌氧氨氧化滤柱初步启动成功.
在第73天,将反应器水力停留时间缩短为1.75 h,此时滤速为0.46 m/h,反应器高负荷运行,进入S2阶段.由于受到高负荷冲击,反应器总氮去除率突然降低,在第73天时,滤柱总氮去除率从82.3%降低为35.2%.随着反应器的运行,微生物适应高水力负荷环境,总氮去除负荷和总氮去除率逐渐上升.第105天时,反应器连续10 d总氮去除率大于75%,总氮去除负荷大于0.8 kg/(m3·d),厌氧氨氧化滤柱有较强活性,反应器启动成功.
在反应器启动过程中,进水COD为20~50 mg/L,碳氮比约为1.Mathava Kumar指出,高碳氮比的污水为基质时,厌氧氨氧化菌会被反硝化细菌代替[8].而本实验特征比稳定在8左右,表明反硝化细菌活性较弱.分析其原因,可能是A/O除磷出水中可生化降解的有机物较少[9].反硝化细菌由于缺少碳源,生长被抑制.而难降解的有机物对厌氧氨氧化菌影响较小[10],因此,在厌氧氨氧化菌和反硝化菌的竞争中占据优势,维持了厌氧氨氧化工艺的稳定.
2.2 常低温厌氧氨氧化工艺运行在S3阶段,反应器进水改为经A/O除磷及亚硝化处理后的城市生活污水.进水亚氮与氨氮之比为0.90~1.40,进水硝氮质量浓度为4~8 mg/L.S3阶段反应器有着很好的氮素去除效果,第106~144天,进水温度在15~20 ℃,总氮去除负荷为0.40~0.50 kg/(m3·d),最大出水总氮为13.4 mg/L,最大出水氨氮质量浓度为4.1 mg/L,氮素排放满足国家城市生活污水一级A排放标准.第144~167天时,运行进入秋季,进水温度降低到15 ℃以下.厌氧氨氧化滤柱氮素去除效果下降,总氮去除率小于70%,出水总氮质量浓度为13~23 mg/L,超过一级A排放标准.
为了提高反应器的氮素去除率,S4阶段将HRT从1.75 h提高到5 h.S4阶段进水温度及出水总氮如图 5所示.可以看出,通过采用延长水力停留时间的方法,提高了总氮去除率.水温为12~15 ℃时,出水氨氮质量浓度为0~2.8 mg/L,总氮质量浓度为9.6~13.7 mg/L,满足了一级A排放标准.反应器总氮去除率大于70%,总氮去除负荷大于0.15 kg/(m3·d),低温条件下使得厌氧氨氧化菌保持了较高的活性.与其他研究成果相比[5, 11],本实验中低温对厌氧氨氧化菌活性影响较小,可能是由于长时间在环境温度下驯化的结果.
Figure 5
![点击查看原图](http://hit.alljournals.cn/html/hitxb_cn/2018/8/PIC/hebgydxxb-50-8-8-5.jpg)
Youpeng Chen指出,进水无机碳(IC)质量浓度大于50 mg/L时会提高厌氧氨氧化菌活性[12].Jiachun Yang将IC与H4+-N比设定为1左右时,取得了较高的厌氧氨氧化活性[13].因此,S5阶段,为了提高低温时反应器的处理效果,在基质中投加125 mg/L的NaHCO3,此时IC质量浓度大于50 mg/L.S5阶段进水IC如图 5所示.可以看出,投加NaHCO3以后整个阶段反应器的总氮去除率较为稳定,最大出水氨氮和总氮质量浓度分别为1.4和13.6 mg/L,小于国家一级A标准.投加IC之前,反应器的总氮去除负荷在0.16 kg/(m3·d)左右,投加IC后,总氮去除负荷稳定在0.22 kg/(m3·d),提高了40%.由此可见,投加无机碳源使反应器在低温条件下取得了良好的运行效果.
从图 4可以看出,S3~S5阶段反应器特征比逐渐升高.S3阶段初期平均特征比为7.95,S4和S5阶段末期平均特征比为8.79和9.83,表明反硝化细菌活性逐渐增强.有研究表明,低温时反硝化细菌会取代厌氧氨氧化菌成为优势菌种[14].而在本实验中,低温下氮素去除基本满足厌氧氨氧化方程式,同时氨氮去除率大于90%,表明反应器主要脱氮途径仍为厌氧氨氧化,10~12 ℃的低温不会破坏厌氧氨氧化和反硝化的共生系统.
2.3 生物学特性研究为了研究不同阶段滤料表面微生物的活性,取滤料进行分析.每次取等量距底部10、30、50、70 cm的滤料,测定滤料表面平均生物膜厚度及微生物活性,结果如图 6所示.可以看出,在反应器运行过程中,生物膜厚度不断增加.反应器在S2阶段生物膜厚度增长较快.可能是由于缩短了HRT,进水总氮负荷增加,有利于生物膜的生长.在S3阶段,由于进水基质质量浓度减小一半,反应器细菌生长受限,生物膜厚度增加较慢.在S4和S5阶段,由于低温的影响,细菌活性受到影响,生物膜增长较慢.反应器在第240天时,厌氧氨氧化菌生物膜厚度为113 μm,超过了同类相关报道[15, 16].与其他细菌形成的生物膜相比[6, 17],厌氧氨氧化生物膜更厚.一方面厌氧氨氧化菌可以分泌大量胞外多聚物,更易于实现自固定[18],另一方面,厌氧氨氧化菌与基质亲和力高[19],虽然生物膜存在传质阻力,但生物膜内部低质量浓度的基质仍然可以维持厌氧氨氧化菌的生长.
Figure 6
![点击查看原图](http://hit.alljournals.cn/html/hitxb_cn/2018/8/PIC/hebgydxxb-50-8-8-6.jpg)
由于反应速率测定时的温度、基质浓度均相同,反应速率代表了污泥中厌氧氨氧化菌和反硝化细菌所占比例.S1和S2阶段,进水为经A/O除磷后的生活污水,氨氮和亚氮质量浓度为45~55 mg/L.高质量浓度的亚硝酸盐对大部分微生物有抑制作用[20],该环境有利于厌氧氨氧化菌同其他微生物的竞争,因此,S1和S2阶段厌氧氨氧化速率较高.S3和S4阶段厌氧氨氧化速率有所降低,原因可能是反应器运行过程中进水温度降低,厌氧氨氧化菌对温度变化较为敏感[21].S5阶段投加了无机碳,厌氧氨氧化速率有了明显的提高,表明低温环境投加无机碳可以提高厌氧氨氧化性能,强化反应器的氮素去除效果.
S1~S2阶段,反硝化速率较低.S4和S5阶段,反硝化速率有所提高,与反应器特征比的升高相符,表明低温条件有利于反硝化细菌的竞争.S1~S5阶段,反硝化均处于较低水平.厌氧氨氧化工艺在实际应用过程中,不会出现反硝化菌取代厌氧氨氧化菌的现象,厌氧氨氧化工艺运行稳定.
3 结论1) 在15~21 ℃的常温条件下,向污水处理厂A/O除磷工艺出水中投加50 mg/L亚硝酸钠作为基质,105 d成功启动了厌氧氨氧化生物滤柱.
2) 进水温度为15~20 ℃时,最大出水氨氮和总氮质量浓度为4.1和13.4 mg/L,可满足国家一级A排放标准.进水温度为12~15 ℃时,厌氧氨氧化菌活性下降,采用延长水力停留时间的方法实现污水处理达标.
3) 冬季水温降低到10~12 ℃时,在进水投加125 mg/L碳酸氢钠,总氮去除负荷提高了40%,最大出水氨氮和总氮质量浓度为1.4和13.6 mg/L,冬季出水氮素达标,实现了厌氧氨氧化工艺在冬季的高效运行.
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