趙 冰,柳曉燕,李勝紅,朱芬芬

污泥基生物炭提升活性污泥系統(tǒng)處理性能

趙 冰,柳曉燕,李勝紅,朱芬芬*

(中國人民大學(xué)環(huán)境學(xué)院,北京 100872)

對(duì)污泥基生物炭提升活性污泥系統(tǒng)處理性能進(jìn)行探討,將活性炭和污泥基生物炭分別投入A2O工藝厭氧池活性污泥,發(fā)現(xiàn)其對(duì)COD削減率最高分別為72.9%和41.1%,均能有效削減,生物炭對(duì)TN削減率最高為74.1%,優(yōu)于活性炭.表征顯示污泥基生物炭上更易附著活性污泥且比表面積更大.在A2O小試厭氧池中以“1次/污泥齡”為頻率投加活性炭、污泥基生物炭和脫脂污泥基生物炭,結(jié)果發(fā)現(xiàn):投加污泥基生物炭對(duì)COD、TN、TP的削減均優(yōu)于活性炭,投加脫脂污泥基生物炭對(duì)COD、TN的削減與投加活性炭相當(dāng),對(duì)TP平均削減率高達(dá)85.6%,優(yōu)于活性炭,表明生物炭處理(BT)工藝比粉末活性炭處理(PACT)工藝處理生活污水能力更強(qiáng),脫脂污泥基生物炭作為污泥脂質(zhì)提取后的副產(chǎn)品更經(jīng)濟(jì).

污泥基生物炭；活性污泥系統(tǒng)；PACT工藝；A2O小試

隨著我國城鎮(zhèn)化水平不斷提高,城鎮(zhèn)設(shè)施建設(shè)不斷完善,污水處理量逐年增加.為使污水處理后達(dá)標(biāo)排放,滿足回用水要求,各地方污水處理廠均開展提標(biāo)改造,以應(yīng)對(duì)水量和水質(zhì)兩方面處理需求.當(dāng)前約有90%的污水處理廠建設(shè)了三級(jí)深度處理設(shè)施[1].在提標(biāo)改造過程中暴露出許多問題,如污泥活性低時(shí)易沉降,污水處理效率低,混合液懸浮固體(MLSS)和溶解氧(DO)濃度升高,不利于脫氮除磷[2].有毒有害有機(jī)微污染物在生化處理段去除效率普遍較低,需添加多種藥劑以調(diào)節(jié)水質(zhì),增加了污水處理廠運(yùn)營成本,與可持續(xù)發(fā)展理念相違背[3-6].現(xiàn)有粉末活性炭處理(PACT)工藝是通過將粉末活性炭加入到污水處理工藝的生化段,使粉末活性炭與活性污泥相互作用,以增強(qiáng)對(duì)污染物的去除效率[7].目前主要應(yīng)用在印染廢水、滲濾液等工業(yè)廢水的處理.國外也有運(yùn)用PACT工藝處理市政污水的實(shí)際案例[7-9].雖然污染物去除效果顯著,但粉末活性炭價(jià)格較貴,污水處理成本會(huì)有所增加.生物炭的相關(guān)研究與應(yīng)用是近年來的熱點(diǎn),在水質(zhì)凈化、土壤改良等領(lǐng)域有經(jīng)濟(jì)高效的特點(diǎn),以污泥為原料制備的污泥基生物炭比商用活性炭的綜合潛力更大,一方面原材料獲取方便且經(jīng)濟(jì),另一方面對(duì)固體廢棄物污泥本身進(jìn)行了資源化處理,同時(shí)可節(jié)省污泥后續(xù)處理成本[10].本研究選取需進(jìn)行處理處置的城鎮(zhèn)污泥為原料制備生物炭,以污泥基生物炭和脫脂污泥基生物炭代替煤質(zhì)、椰殼或木屑制備的傳統(tǒng)粉末活性炭,構(gòu)建新型生物炭處理(BT)工藝,采用間歇投加方式,分析其在實(shí)際工程中運(yùn)行的可能性,期望對(duì)相關(guān)工藝和工程技術(shù)提供理論依據(jù).

1 材料與方法

1.1 材料

取北京市某污水處理廠料倉污泥(含水率為80%～86%),烘干粉碎后過20目篩.采用索氏提取法進(jìn)行脫脂.將10g用濾紙包裹的干污泥置于索氏提取器中,將400mL正己烷和乙醇的混合液(體積比為1:1)加入提取瓶,于80℃條件下水浴加熱8～12h.濾紙中剩余固體即為脫脂污泥[11].將經(jīng)過預(yù)處理的污泥和脫脂污泥分別置于管式爐中,在500℃條件下進(jìn)行絕氧熱解,升溫速率為5～10℃/min,恒溫1h,最終分別得到污泥基生物炭(SBB)和脫脂污泥基生物炭(DSBB).活性炭為市售粉末活性炭(AC,粒徑為200目).

1.2 試驗(yàn)方法

1.2.1 燒杯實(shí)驗(yàn)方法 從圖1所示的A2O小試裝置取100mL新鮮厭氧池活性污泥于300mL燒杯中,設(shè)計(jì)AC和SBB的投加量3個(gè)梯次,分別為0.05,0.10和0.20g,反應(yīng)時(shí)間分別為0.5,1.0和2.0h,組合后得到9組實(shí)驗(yàn)樣本,反應(yīng)條件設(shè)置情況如表1所示.取厭氧池活性污泥不添加碳基材料,僅攪拌,其他條件保持一致.隨后將混合液通過離心過濾,測定反應(yīng)前厭氧池活性污泥水相和反應(yīng)后混合液濾液中的COD、TN和TP,以比較AC、SBB在燒杯實(shí)驗(yàn)中與污泥的協(xié)同作用效果.對(duì)反應(yīng)后的厭氧池活性污泥、(活性污泥+AC)混合樣和(活性污泥+SBB)混合樣進(jìn)行表征.利用熒光顯微鏡BK-FL和場發(fā)射掃描電子顯微鏡(SEM) SU8200測定微觀形貌特征;利用麥克ASAP2020比表面積測定儀測定比表面積、孔容孔徑等;利用傅立葉紅外光譜儀測定表面官能團(tuán),其中采用Perkin Elmer Frontier型號(hào)紅外光譜儀測定活性污泥及其與碳基吸附劑作用后樣品,采用VERTEX 70型號(hào)光譜儀測定SBB.

1.2.2 A2O小試實(shí)驗(yàn)方法 從北京市某污水處理廠曝氣池取20L泥樣,進(jìn)行馴化培養(yǎng),培養(yǎng)期約30d.A2O系統(tǒng)pH值為6.7～6.9.厭氧池、缺氧池和好氧池的DO濃度分別為0.7,1.1和3.6mg/L,MLSS分別為3004,2892和2953mg/L.污泥負(fù)荷為0.15kg BOD5/(kgMLSS·d),污泥停留時(shí)間為15d.C/N=6,C/P= 40.進(jìn)水流量速率為1.67L/h,水力停留時(shí)間為8.88h.污泥外回流比為100%,內(nèi)回流比為200%.

圖1 A2O小試裝置運(yùn)行示意

表1 反應(yīng)條件設(shè)置情況

本研究設(shè)計(jì)運(yùn)行2個(gè)規(guī)格相同的A2O小試裝置,材料均為有機(jī)玻璃,裝置結(jié)構(gòu)如圖1所示.單個(gè)池體體積為4.5L,總有效體積為22.5L.以實(shí)驗(yàn)室藥劑配水模擬市政生活污水作為污水來源,以葡萄糖為有機(jī)碳源,濃度為0.41g/L;以氯化銨為氮源,濃度為0.19g/L;以磷酸二氫鉀為磷源,濃度為0.03g/L,以碳酸氫鈉為無機(jī)碳源,同時(shí)起調(diào)節(jié)pH值的作用,濃度為0.08g/L.AC、SBB、DSBB的投加方式為間歇投加、投加頻率為1次/污泥齡.

根據(jù)《水質(zhì)化學(xué)需氧量的測定快速消解分光光度法(HJ/T399-2007)》[12],采用一體型三參數(shù)測定儀(5B-6C,北京連華)測定水樣COD濃度值.根據(jù)《水質(zhì)總氮的測定堿性過硫酸鉀消解紫外分光光度法(HJ636-2012)》[13]和《水質(zhì)總磷的測定鉬酸銨分光光度法(GB/T11893-1989)》[14]分別測定水樣TN和TP,TN在波長220和275nm下測定吸光度值,按式(1)計(jì)算校正吸光度值,TP在波長700nm下測定吸光度值,分別代入各自校準(zhǔn)曲線得出濃度值.按公式(2)計(jì)算削減率,用Origin軟件繪制濃度圖和削減率圖.

=220-2×275(1)

式中:為校正吸光度值;220為波長220nm下測定的吸光度值;275為波長275nm下測定的吸光度值.

=(0-)÷0×100% (2)

式中:為削減率,%;0為投加碳基吸附劑前的背景濃度值,mg/L;為濃度值,mg/L.

2 結(jié)果與討論

2.1 燒杯實(shí)驗(yàn)探討B(tài)T工藝的可行性

2.1.1 投加量和反應(yīng)時(shí)間的影響 將AC和SBB置于蒸餾水中會(huì)產(chǎn)生浸出污染物,為使實(shí)驗(yàn)數(shù)據(jù)準(zhǔn)確,首先進(jìn)行污染物浸出實(shí)驗(yàn),得到的污染物浸出值作為背景值,并在計(jì)算中減掉背景值可得污染物實(shí)際值,結(jié)果表明AC和SBB浸出COD值分別為(107.50±54.20)mg/L和(88.80±37.20)mg/L,浸出TN幾乎為0.

AC和SBB對(duì)COD削減情況如圖2所示,可以看出,AC比SBB對(duì)COD去除效果更好.從投加量看,AC對(duì)COD去除效果最佳的投加量為0.05g,其次為0.1g,最差為0.2g;SBB對(duì)COD去除效果最佳的投加量為0.1g(以活性污泥樣體積計(jì)算為1000mg/L,下同),其次為0.2g,最差為0.05g,但整體相差不大,表明AC在對(duì)COD去除過程中投加量較少可產(chǎn)生較好去除效果,隨著投加量增加會(huì)抑制對(duì)COD的去除.從反應(yīng)時(shí)間看,AC和SBB對(duì)COD去除效果最佳的反應(yīng)時(shí)間均為0.5h,其次均為2.0h,最差為1.0h.且AC和SBB對(duì)COD去除效果最好的條件分別為0.10g+ 0.5h和0.10g+1.0h.

AC和SBB對(duì)TN削減情況如圖3所示,可以看出AC對(duì)TN幾乎無去除效果,而SBB對(duì)TN有較好去除效果,削減率最高為74.1%.從投加量看,SBB投加量為0.05和0.2g時(shí)對(duì)TN去除效果較好,削減率均能達(dá)到35%.從反應(yīng)時(shí)間看,AC和SBB對(duì)TN去除效果最佳的反應(yīng)時(shí)間分別為2.0和1.0h,最差均為0.5h,推測SBB和活性污泥協(xié)同作用去除TN在1.0～2.0h達(dá)到飽和.SBB對(duì)TN去除效果最好的反應(yīng)條件為0.20g+1.0h.

2.1.2 燒杯實(shí)驗(yàn)反應(yīng)后混合樣的表征分析 (1)熒光顯微鏡及SEM結(jié)果與分析

為探究碳基材料與活性污泥的耦合協(xié)同作用機(jī)理,將添加了碳基材料的混合樣品和活性污泥進(jìn)行表征分析,根據(jù)上述投加量和反應(yīng)時(shí)間的探討,確定AC、SBB的投加量均為1000mg/L樣品,攪拌時(shí)間為1.0h,此條件下SBB對(duì)COD去除效果最好,對(duì)TN去除效果也較好.

圖2 投加量和反應(yīng)時(shí)間對(duì)COD的影響

反應(yīng)條件見表1,下同

圖3 投加量和反應(yīng)時(shí)間對(duì)TN的影響

將得到的混合樣品置于熒光顯微鏡下放大40倍觀察,如圖4所示.結(jié)果表明,活性污泥經(jīng)過攪拌后呈現(xiàn)出較為均勻的分布狀態(tài),添加AC后,呈現(xiàn)出較為明顯的分離狀態(tài),AC上附著的活性污泥較少;添加SBB后,呈現(xiàn)較活性污泥稍差的分布狀態(tài),推測SBB對(duì)活性污泥具有較好的附著性,大部分碳粒被活性污泥附著包裹.

根據(jù)掃描電鏡(放大倍數(shù)為10k)結(jié)果,如圖5所示,可得上述相似結(jié)論.與添加AC相比,活性污泥和添加SBB后的表觀更為相似,均具有相對(duì)平滑緊密的結(jié)構(gòu),印證了添加SBB的條件下,活性污泥可以得到更好附著.周穎[15]的研究表明果殼生物炭表面生物膜結(jié)構(gòu)較為緊密,與本文結(jié)果一致.

圖4 活性污泥及其與碳基吸附劑作用后的顯微鏡觀測

圖5 活性污泥及其與碳基吸附劑作用后的SEM圖

(2)BET檢測結(jié)果與分析

BET檢測結(jié)果如表2所示,活性污泥添加SBB與添加AC得到的混合材料相比,比表面積、孔體積、平均孔徑均差別不大,且孔體積均大于活性污泥.添加了AC和SBB混合材料的比表面積分別為1.1988和1.3389m2/g,未添加碳基材料的活性污泥比表面積為0.1153m2/g,反應(yīng)后的混合材料比表面積比活性污泥大了約10倍,且AC和SBB比表面積分別為1000和13.5260m2/g,反應(yīng)后的混合材料比表面積急劇變小,表明AC和SBB對(duì)活性污泥具有附著性.

(3)紅外光譜表征結(jié)果

活性污泥及其碳基材料反應(yīng)后混合樣的紅外光譜如圖6所示,活性污泥的特征波峰分別為波數(shù)為3300的O-H伸縮振動(dòng),1700的C=C伸縮振動(dòng)及1050的C-O伸縮振動(dòng),添加AC和SBB后混合樣紅外光譜圖在特征波數(shù)3300、1700、1050表現(xiàn)出相同波峰,且3個(gè)樣品紅外光譜圖相似,表明活性污泥在AC和SBB表面附著性強(qiáng).

表2 活性污泥及其與碳基吸附劑作用后的BET檢測結(jié)果

圖6 活性污泥及其與碳基吸附劑作用后的紅外光譜圖

2.2 小試裝置探討B(tài)T工藝處理生活污水可行性分析

2.2.1 BT與PACT工藝出水COD對(duì)比 采用PACT工藝處理制藥廢水的小試研究中,反應(yīng)器中AC的投加量為1500mg/L時(shí),出水中COD的去除率明顯降低[16].但是考慮到工藝和污水背景,此次實(shí)驗(yàn)設(shè)計(jì)投加量較工業(yè)廢水小,設(shè)計(jì)投加量為4.5g或3.0g.投加AC、SBB、DSBB后,A2O小試系統(tǒng)出水COD的變化如圖7所示.投加活性炭和生物炭后,COD濃度在10d中均小于投加前的背景值.除投加4.5gSBB外,在10d的出水檢測結(jié)果中,其余投加組COD濃度均低于城鎮(zhèn)污水處理廠污染物一級(jí)A標(biāo)準(zhǔn)限值.投加4.5gAC對(duì)COD的去除效果較為明顯,削減率為35.1%～63.6%,A2O小試裝置運(yùn)行較為平穩(wěn).投加4.5gSBB后,運(yùn)行10d的平均削減率為37.0%,但COD濃度在30～80mg/L間反復(fù),運(yùn)行期間仍有5d遠(yuǎn)超出一級(jí)A標(biāo)準(zhǔn)限值.這可能是由于投加4.5gSBB前COD背景值過高,且其余組實(shí)驗(yàn)溫度均為16～20℃之間,該組為8～10℃,實(shí)驗(yàn)時(shí)環(huán)境溫度過低,影響了污泥活性所致[17-18].投加3.0gSBB的結(jié)果顯示,COD濃度基本維持在20～30mg/L,COD削減率最高可達(dá)79.7%,最低為55.2%,除運(yùn)行5d時(shí)COD濃度略高于準(zhǔn)四類水標(biāo)準(zhǔn)外,其余9d均可達(dá)到準(zhǔn)四類水標(biāo)準(zhǔn).投加4.5gDSBB后,COD濃度基本維持在10～30mg/L,COD削減率為27.7%～75.2%.總體來看, 10d COD平均削減率投加4.5gSBB組低于4.5gAC組,投加4.5gDSBB組與4.5gAC組差別不大,投加3.0gSBB組高于4.5gAC組.綜上所述,相同溫度條件下,投加生物炭可以達(dá)到投加活性炭時(shí)對(duì)COD的去除效果.

圖7 BT與PACT工藝的COD對(duì)比

2.2.2 BT與PACT工藝出水TN對(duì)比 如圖8所示,除投加4.5gSBB外,其余投加活性炭及生物炭后的TN濃度均小于投加前的背景值.PACT工藝運(yùn)行中,TN僅有第1d出水的檢測結(jié)果低于城鎮(zhèn)污水處理廠污染物一級(jí)A標(biāo)準(zhǔn)和一般地區(qū)準(zhǔn)四類水標(biāo)準(zhǔn)限值,但TN削減率最高可達(dá)57.1%,最低為24.0%.投加4.5gSBB后前期TN去除效果較好,在第4d時(shí)TN濃度最低,TN削減率達(dá)到88.2%.但是從第5d開始,出水TN均高于未投加時(shí).原因可能為SBB投加到活性系統(tǒng)中起到的吸附作用較小,主要是作為微生物載體,提供更多微生物附著位點(diǎn),增強(qiáng)微生物活性和對(duì)環(huán)境的耐受性,以達(dá)到去除污染物的目的[19-21].結(jié)合A2O系統(tǒng)脫氮除磷原理,投加SBB后,微生物濃度獲得附著位點(diǎn),濃度增加,導(dǎo)致后期微生物群落間出現(xiàn)競爭關(guān)系.一方面是氧氣競爭,導(dǎo)致好氧池中硝化細(xì)菌活性降低,硝化反應(yīng)減弱,因此后期對(duì)TN的去除效果減弱;一方面是碳源競爭,導(dǎo)致A2O小試系統(tǒng)穩(wěn)定性降低.投加3.0gSBB對(duì)TN削減效果明顯,TN濃度前8d均符合一級(jí)A標(biāo)準(zhǔn)及一般地區(qū)準(zhǔn)四類水標(biāo)準(zhǔn),其中有3d符合水體富營養(yǎng)化問題突出地區(qū)的準(zhǔn)四類水標(biāo)準(zhǔn).投加4.5gDSBB后,TN濃度有7d符合一級(jí)A標(biāo)準(zhǔn)和一般地區(qū)準(zhǔn)四類水標(biāo)準(zhǔn),TN削減率為14.3%～ 56.5%.總體來看,10d TN平均削減率情況與COD相似,投加4.5gSBB組最低,投加4.5gDSBB組略低于4.5gAC組,投加3.0gSBB組高于4.5gAC組.綜上所述,相同溫度條件下,投加生物炭可以達(dá)到投加活性炭時(shí)對(duì)TN的去除效果.

圖8 BT與PACT工藝的TN對(duì)比

2.2.3 BT與PACT工藝出水TP對(duì)比 如圖9所示,投加4.5gAC后和投加4.5gSBB后,TP的濃度均未低于城鎮(zhèn)污水處理廠污染物一級(jí)A標(biāo)準(zhǔn)及準(zhǔn)四類水標(biāo)準(zhǔn)限值.與TN變化情況一致,除投加4.5gSBB外,其余投加活性炭及生物炭后的TP濃度均小于投加前的背景值.投加4.5gAC后,TP削減率為18.0%～73.7%,去除效果好于TN.投加4.5gSBB后,后期5～10d的TP去除效果好于前期的1～4d.投加3.0gSBB后,TP削減率均超過80%.投加4.5gDSBB后,TP削減率均超過75%,COD、TN和TP的濃度隨時(shí)間推進(jìn)均呈現(xiàn)先降低后增加的趨勢,可能是在投加DSBB后,由于管道堵塞等裝置運(yùn)行原因,DSBB與活性污泥混合不充分所致[22-24].總體來看,10d TP平均削減率大小順序與COD和TN一致,投加4.5gSBB組最低,其次是投加4.5gAC組、投加4.5gDSBB組,投加3.0gSBB組最高,證明了溫度確實(shí)會(huì)對(duì)活性污泥系統(tǒng)產(chǎn)生影響[25].投加4.5gSBB后對(duì)TP去除效果較差,而投加3.0gSBB后效果很好,可能由于厭氧環(huán)境下聚磷菌只能利用污水中的易降解有機(jī)污染物作為碳源滿足自身需求,但該裝置中葡萄糖為唯一碳源,可能在厭氧池已經(jīng)存在反硝化菌和聚磷菌的競爭.由圖9還可以看出,投加4.5gDSBB組10d TP平均削減率與3.0gSBB組差別不大,并遠(yuǎn)高于4.5gAC組. Yang等[26]綜述了生物炭在水資源回收中的應(yīng)用,Zhang等[27]對(duì)生物炭及其改性物去除水中磷酸鹽進(jìn)行評(píng)價(jià),均表明生物炭具備有效的捕磷能力,通常受其物理化學(xué)參數(shù)影響,表面的有機(jī)官能團(tuán)有助于增強(qiáng)靜電引力,促進(jìn)磷吸附. Kizito等[28]利用木頭、玉米棒、稻殼、鋸末制備的生物炭從厭氧消化液中回收磷酸鹽,結(jié)果表明回收能力分別為7.67mg/g、6.43mg/g、5.73mg/g、5.41mg/g,本研究中3.0gSBB和4.5gDSBB組的回收能力平均分別為13.10mg/g、13.78mg/g,優(yōu)于Kizito等人.綜上所述,相同溫度條件下,投加生物炭對(duì)TP的去除效果遠(yuǎn)好于投加活性炭.原因?yàn)橥都覵BB或DSBB后,A2O小試裝置厭氧池、缺氧池和好氧池中的污泥濃度增加,為維持原定約15d的污泥停留時(shí)間,增加了排泥量,進(jìn)而增加溶解性磷元素隨剩余污泥的排出量,導(dǎo)致出水中TP濃度顯著降低[29-30].

圖9 BT與PACT工藝的TP對(duì)比

3 結(jié)論

3.1 燒杯實(shí)驗(yàn)結(jié)果表明,活性炭和污泥基生物炭均能對(duì)COD產(chǎn)生較好去除效果,且污泥基生物炭對(duì)TN去除效果更好,更容易被活性污泥附著.AC和SBB對(duì)COD削減率最高值分別為72.9%和41.1%,對(duì)TN削減率最高值分別為8.3%和74.1%.

3.2 小試裝置結(jié)果表明,BT工藝比PACT工藝具有更強(qiáng)的處理生活污水能力,脫脂污泥基生物炭比污泥基生物炭更經(jīng)濟(jì).生活污水中投加4.5gAC、3.0gSBB和4.5gDSBB后,COD削減率分別為35.1%～63.6%、55.2%～79.7%和27.7%～75.2%,TN削減率分別為24.0%～57.1%、18.3%～66.6%和14.3%～ 56.5%,TP削減率分別為18.0%～73.7%、81.4%～ 92.5%和75.8%～90.1%.因此,污泥基生物炭能夠提升活性污泥系統(tǒng)處理能力.

[1] 張 龍,涂 勇,吳 偉,等.生物活性炭(PACT)對(duì)印染廢水A2O工藝強(qiáng)化運(yùn)行效果的表征 [J]. 環(huán)境科學(xué)學(xué)報(bào), 2014,34(3):664-670.

Zhang L, Tu Y, Wu W, et al. Characterization of improved performance by powdered active carbon treatment (PACT) for dyeing wastewater treatment using A2O process [J]. Acta Scientiae Circumstantiae, 2014,34(3):664-670.

[2] Ben W W, Zhu B, Yuan X J, et al. Occurrence, removal and risk of organic micropollutants in wastewater treatment plants across China: Comparison of wastewater treatment processes [J]. Water Research, 2018,130:38-46.

[3] Jiang J Q, Yin Q, Zhou J L, et al. Occurrence and treatment trials of endocrine disrupting chemicals (EDCs) in wastewaters [J] Chemosphere, 2005,61(4):544-550.

[4] Yang G, Zhang G M, Wang H C, Current state of sludge production, management, treatment and disposal in China [J]. Water Research, 2015,78:60-73.

[5] 董 儀,朱芬芬,張榮巖,等.城鎮(zhèn)污泥中神經(jīng)酰胺的分離純化 [J]. 中國環(huán)境科學(xué), 2019,39(5):2063-2070.

Dong Y, Zhu F F, Zhang R Y, et al. Preliminary study on extraction and purification of ceramide in sewage sludge [J]. China Environmental Science, 2019,39(5):2063-2070.

[6] 郭明帥,王 菲,張學(xué)良,等.改性生物炭活化過硫酸鹽對(duì)水中苯和氯苯的去除機(jī)制 [J]. 中國環(huán)境科學(xué), 2020,40(12):5280-5289.

Guo M S, Wang F, Zhang X L, et al. Removal mechanism of benzene and chlorobenzene in water by modified biochar activates persulfate [J]. China Environmental Science, 2020,40(12):5280-5289.

[7] Wu W, Zhang L, Chen Y, et al. Interaction between activated carbon and microorganisms in PACT process [J]. The Canadian Journal of Chemical Engineering, 2014,92(8):1340-1345.

[8] Fernández-Bou á S, Nascentes A L, Pereira B C, et al. Mathematical modeling of COD removal via the combined treatment of domestic wastewater and landfill leachate based on the PACT process [J]. Journal of Environmental Science & Health Part A, 2015,50(4):378- 384.

[9] (土)費(fèi)爾漢·切森,(土)厄茲古爾·阿克塔斯.吸附生化耦合水處理技術(shù):原理與應(yīng)用 [M]. 北京:化學(xué)工業(yè)出版社, 2019:94-105.

Ferhan ?, ?zgür A. Activated carbon for water and waste water treatment: Integration of absorpotion and biological treatment [M]. Beijing: Chemical Industry Press, 2019:94-105.

[10] Lee S E, Shin H S, Paik B C. Treatment of Cr(VI)-containing wastewater by addition of powdered activated carbon to the activated sludge process [J]. Water Research, 1989,23(1):67-72.

[11] Zhu F F, Zhao L Y, Zhang Z L, et al. Preliminary study at lipids extraction technology from municipal sludge by organic solvent [J]. Procedia Environmental Sciences, 2012,16:352-356.

[12] HJ/T399-2007 水質(zhì)化學(xué)需氧量的測定快速消解分光光度法[S].

HJ/T399-2007 Water quality-Determination of the chemical oxygen demand-Fast digestion-Spectrophotometric method [S].

[13] HJ636-2012 水質(zhì)總氮的測定堿性過硫酸鉀消解紫外分光光度法[S].

HJ636-2012 Water quality-Determination of total nitrogen-Alkaline potassium persulfate digestion UV spectrophotometric method [S].

[14] GB/T11893-1989 水質(zhì)總磷的測定鉬酸銨分光光度法[S].

GB/T11893-1989 Water quality-Determination of total phosphorus- Ammonium molybdate spectrophotometric method [S].

[15] 周 穎.炭基強(qiáng)化生物滲濾系統(tǒng)處理雨水排水口出水的性能研究 [D]. 杭州:浙江大學(xué), 2021.

Zhou Y. Study on performance of biochar-enhanced biofiltration system for stormwater runoff purification [D]. Hangzhou: Zhejiang University, 2021.

[16] Eckenfelder W W, Argaman Y, Miller E. Process selection criteria for the biological treatment of industrial wastewaters [J]. Environmental Progress, 1989,8(1):40-45.

[17] Martini S, Afroze S, Roni K A. Modified eucalyptus bark as a sorbent for simultaneous removal of COD, oil, and Cr (III) from industrial wastewater [J]. Alexandria Engineering Journal, 2020,59(3):1637- 1648.

[18] Nguyen Q, Watari T, Yamaguchi T, et al. COD removal from artificial wastewater by electrocoagulation using aluminum electrodes [J]. International Journal of Electrochemical Science, 2020,15:39-51.

[19] 馬鋒鋒,趙保衛(wèi),刁靜茹,等.磁性生物炭對(duì)水體中對(duì)硝基苯酚的吸附特性 [J]. 中國環(huán)境科學(xué), 2019,39(1):170-178.

Ma F F, Zhao B W, Diao J R, et al. Adsorption characteristics of p-nitrophenol removal by magnetic biochar [J]. China Environmental Science, 2019,39(1):170-178.

[20] 馬志強(qiáng),胥思勤,姬江浩,等.改性水稻生物炭對(duì)水體中Sb(Ⅲ)的吸附 [J]. 中國環(huán)境科學(xué), 2021,41(6):11.

Ma Z Q, Xu S Q, Ji J H, et al. Adsorption of Sb(Ⅲ) in water by modified rice straw biochar [J]. China Environmental Science, 2021, 41(6):11.

[21] 魏嘯楠,張 倩,李 孟,等.磷酸改性生物炭負(fù)載硫化錳去除廢水中重金屬鎘 [J]. 中國環(huán)境科學(xué), 2020,40(5):2095-2102.

Wei X N, Zhang Q, Li M, et al. Removal of cadmium in wastewater by phosphoric acid modified biochar supported manganese sulfide [J]. China Environmental Science, 2020,40(5):2095-2102.

[22] Xin W, Song Y, Wu Y. Enhanced capture ability of sludge-derived mesoporous biochar with a template-like method [J]. Langmuir 2019,35(18):6039-6047.

[23] 李勝紅,朱芬芬.原污泥與脫脂污泥制備生物炭的比較及其特性分析 [J]. 環(huán)境工程, 2021,39(9):154-159.

Li S H, Zhu F F. Comparison and characteristics of biochar by sludge and degreasing-sludge [J]. Environmental Engineering, 2021,39(9): 154-159.

[24] Regkouzas P, Diamadopoulos E. Adsorption of selected organic micro-pollutants on sewage sludge biochar [J]. Chemosphere, 2019, 224(6):840-851.

[25] Gan Q, Hou H, Liang S, et al. Sludge-derived biochar with multivalent iron as an efficient Fenton catalyst for degradation of 4-Chlorophenol [J]. Science of The Total Environment, 2020,725: 138299.

[26] Yang H L, Ye S J, Zeng Z T, et al. Utilization of biochar for resource recovery from water: A review [J]. Chemical Engineering Journal, 2020,397:125502.

[27] Zhang M, Song G, Gelardi D L, et al. Evaluating biochar and its modifications for the removal of ammonium, nitrate, and phosphate in water [J]. Water Research, 2020,186:116303.

[28] Kizito S, Luo H, Wu S, et al. Phosphate recovery from liquid fraction of anaerobic digestate using four slow pyrolyzed biochars: Dynamics of adsorption, desorption and regeneration [J]. Journal of Environmental Management, 2017,201:260.

[29] Ma Y F, Yang L E, Li Wu, et al. Carbon nanotube supported sludge biochar as an efficient adsorbent for low concentrations of sulfamethoxazole removal [J]. Science of The Total Environment, 2020,718(20):137299.

[30] Gopinath A, Divyapriya G, Srivastava V, et al. Conversion of sewage sludge into biochar: A potential resource in water and wastewater treatment [J]. Environmental Research, 2021,194:110656.

Sludge-based biochar enhances treatment performance of activated sludge systems.

ZHAO Bing, LIU Xiao-yan, LI Sheng-hong, ZHU Fen-fen*

(School of Environment & Natural Resources, Renmin University of China, Beijing 100872, China)., 2022,42(7)：3156～3163

This study investigates the sludge-based biochar to enhance the treatment performance of activated sludge systems. The highest COD reduction rates of 72.9% and 41.1% were found for activated carbon and sludge-based biochar, respectively, into the activated sludge of anaerobic tank in the A2O process. The highest reduction rate of TN was 74.1%, which was more effective than that of activated carbon. Characterization showed that activated sludge was more easily attached to sludge-based biochar and had a larger specific surface area. Activated carbon, sludge-based biochar and defatted sludge-based biochar were added in the anaerobic tank of A2O pilot plant at the frequency of one addition per sludge age. The results showed that adding sludge-based biochar had better reduction effect on COD, TN and TP than adding activated carbon. Compared with the addition of activated carbon, adding defatted sludge-based biochar had little difference in COD and TN reduction, but the average reduction rate of TP was 85.6%, which was more effective than that of activated carbon. In conclusion, biochar treatment (BT) process is more powerful than powdered activated carbon treatment (PACT) process in treating domestic sewage, and defatted sludge-based biochar is more economical as a by-product of sludge lipid extraction.

sludge-based biochar；activated sludge system；PACT process；A2O small scale test

X705

A

1000-6923(2022)07-3156-08

趙 冰(1994-),女,河北石家莊人,中國人民大學(xué)博士研究生,主要研究方向?yàn)楣腆w廢物處理處置與資源化.發(fā)表論文3篇.

2021-12-16

國家重點(diǎn)研發(fā)計(jì)劃(2019YFC1906501)

* 責(zé)任作者, 教授, zhufenfen@ruc.edu.cn