賀昭銘,劉佳妮,田亞茹,于德爽,苗圓圓*,張文克,馬國(guó)成,趙鑫超,袁 悅

外源全程硝化污泥對(duì)城市污水SPNA系統(tǒng)的影響

賀昭銘1,劉佳妮1,田亞茹1,于德爽1,苗圓圓1*,張文克1,馬國(guó)成1,趙鑫超1,袁 悅2

(1.青島大學(xué)環(huán)境科學(xué)與工程學(xué)院,山東 青島 266071；2.上海市政工程設(shè)計(jì)研究總院(集團(tuán))有限公司,上海 200092)

為強(qiáng)化城市污水短程硝化-厭氧氨氧化(SPNA)系統(tǒng)脫氮性能與穩(wěn)定性,在間歇曝氣條件下研究投加外源全程硝化污泥對(duì)城市污水SPNA系統(tǒng)的影響及機(jī)理.結(jié)果顯示,空白組(SBR3)總氮去除率由35.5%升高至66.3%,短周期分批次投加外源全程硝化污泥(SBR2,投加周期為5d,投加比為2.5%)與長(zhǎng)周期分批次投加(SBR1,投加周期為20d,投加比為10%)的SPNA系統(tǒng)總氮去除率分別由31.7%和36.5%升高至76.3%和67.2%,這表明,投加全程硝化污泥有利于提高SPNA系統(tǒng)的脫氮性能,且當(dāng)投加總量相同時(shí),短周期分批次投加的效果優(yōu)于長(zhǎng)周期分批次投加.功能菌活性結(jié)果與脫氮效果一致,SBR1～SBR3的厭氧氨氧化菌(AnAOB)最大活性分別由3.43mg-N/(L·h)升高至7.66,8.19和7.31mg-N/(L·h),氨氧化細(xì)菌(AOB)與亞硝酸鹽氧化菌(NOB)活性比分別為8.79,9.83和8.78.在間歇曝氣條件下投加全程硝化污泥,可選擇性抑制NOB、富集AOB,提高AOB與NOB的活性比,利于穩(wěn)定短程硝化效果,為AnAOB提供穩(wěn)定的基質(zhì),且短周期分批次投加可降低外源硝化污泥中的NOB對(duì)系統(tǒng)的沖擊,更有利于實(shí)現(xiàn)高AOB與NOB活性比,提高系統(tǒng)穩(wěn)定性.此外,內(nèi)源短程反硝化菌相對(duì)豐度明顯升高,可為AnAOB提供更多的亞硝酸鹽氮,進(jìn)一步利于AnAOB富集.

短程硝化-厭氧氨氧化一體化；生物添加；全程硝化污泥；間歇曝氣；高通量測(cè)序；影響因素

由于城市污水的碳氮比過(guò)低,在傳統(tǒng)的全程硝化-反硝化污水處理工藝中,往往需要添加外碳源強(qiáng)化反硝化效果,使出水的氮濃度達(dá)到排放標(biāo)準(zhǔn).但外加碳源不僅會(huì)給后續(xù)運(yùn)行帶來(lái)一定的壓力,還會(huì)提高運(yùn)行成本[1-2].短程硝化-厭氧氨氧化一體化(SPNA)工藝即在一個(gè)反應(yīng)器中同時(shí)實(shí)現(xiàn)短程硝化和厭氧氨氧化,氨氧化細(xì)菌(AOB)將部分氨氮氧化成亞硝酸鹽氮,隨后厭氧氨氧化菌(AnAOB)將這部分亞硝酸鹽氮與剩余的氨氮轉(zhuǎn)化成氮?dú)夂蜕倭康南跛猁}氮,完成污水脫氮[3-4].該工藝主要脫氮功能菌為自養(yǎng)菌,不需要外加有機(jī)碳源,且只需將約一半的氨氮氧化為亞硝酸鹽氮,因此具有節(jié)省曝氣能耗和有機(jī)碳源、剩余污泥產(chǎn)量少等優(yōu)點(diǎn)[5],有望實(shí)現(xiàn)低能耗城市污水深度脫氮,具有重要意義.

城市污水SPNA工藝的可行性,已初步得到驗(yàn)證,但仍存在諸多難點(diǎn)有待解決.城市污水SPNA工藝的瓶頸是難以有效抑制亞硝酸鹽氧化菌(NOB).由于缺少高游離氨和高游離亞硝酸濃度等抑制NOB的條件,NOB極易大量生長(zhǎng),與AnAOB競(jìng)爭(zhēng)亞硝酸鹽氮[6],一方面,造成城市污水SPNA系統(tǒng)出水硝酸鹽氮濃度升高,脫氮性能惡化;另一方面,可導(dǎo)致AnAOB活性和豐度逐漸下降,加劇系統(tǒng)失穩(wěn).有研究發(fā)現(xiàn),可以通過(guò)控制低溶解氧(DO)濃度和間歇曝氣等條件抑制NOB活性[7-8],但這些條件并不充分,由于NOB大量生長(zhǎng)造成的SPNA系統(tǒng)脫氮性能惡化的現(xiàn)象屢見(jiàn)報(bào)道[9]. Wang等[10]報(bào)道,控制DO在0.10～0.13mg/L并不能有效抑制NOB活性,城市污水SPNA系統(tǒng)出水硝酸鹽氮濃度逐漸升高至18.1mg-N/L;Karol等[11]發(fā)現(xiàn),單純控制間歇曝氣并不能充分抑制NOB活性.利用高游離氨和游離亞硝酸濃度對(duì)SPNA系統(tǒng)中污泥進(jìn)行預(yù)處理,可短期內(nèi)抑制NOB活性,但增大了工藝運(yùn)行復(fù)雜度和運(yùn)行能耗,且長(zhǎng)期運(yùn)行過(guò)程中,NOB可能會(huì)逐漸適應(yīng)高游離氨和游離亞硝酸濃度,導(dǎo)致系統(tǒng)脫氮性能再次下降[12].目前,在城市污水SPNA系統(tǒng)中實(shí)現(xiàn)長(zhǎng)期穩(wěn)定的短程硝化和NOB抑制和淘洗,仍未取得突破性進(jìn)展.

近期研究發(fā)現(xiàn),在城市污水SPNA系統(tǒng)中NOB活性較高的情況下,向其中投加外源全程硝化污泥,未造成系統(tǒng)中NOB活性進(jìn)一步升高和脫氮性能惡化,反而可選擇性提高AOB活性,促進(jìn)AnAOB富集,進(jìn)而提高系統(tǒng)脫氮效果[13].城市污水處理廠普遍采用全程硝化-反硝化工藝處理污水,該工藝會(huì)定期排放大量的剩余污泥,因此,本試驗(yàn)采用的外源全程硝化污泥在污水廠非常常見(jiàn),具有通用性和普遍性,研究其對(duì)SPNA工藝的促進(jìn)效果和機(jī)理具有一定的借鑒意義,該方法有望突破城市污水SPNA工藝的瓶頸,促進(jìn)該工藝的推廣應(yīng)用.但外源全程硝化污泥對(duì)城市污水SPNA系統(tǒng)脫氮性能的影響機(jī)理尚未明了,且外源全程硝化污泥的投加量與投加周期也需要進(jìn)一步優(yōu)化,值得進(jìn)一步研究.

1 材料與方法

1.1 試驗(yàn)裝置與運(yùn)行方式

利用SBR反應(yīng)器構(gòu)建城市污水SPNA系統(tǒng).平行運(yùn)行3個(gè)反應(yīng)器SBR1,SBR2和SBR3,有效容積為3L,排水比為50%.通過(guò)溫控裝置使反應(yīng)器溫度維持在32℃;通過(guò)機(jī)械攪拌器進(jìn)行攪拌;通過(guò)微型曝氣泵進(jìn)行曝氣;通過(guò)轉(zhuǎn)子流量計(jì)調(diào)節(jié)曝氣量(圖1).反應(yīng)器采用前置缺氧攪拌的間歇曝氣方式運(yùn)行,間歇曝氣的周期通過(guò)繼電器調(diào)控,其中前置缺氧攪拌時(shí)間為40min,隨后按照好氧9min/缺氧21min方式運(yùn)行,曝氣階段DO濃度控制在0.5～0.8mg/L.

圖1 反應(yīng)器裝置示意

表1 各試驗(yàn)階段運(yùn)行條件

試驗(yàn)共分為3個(gè)階段(表1):階段Ⅰ(1～58d),不投加外源全程硝化污泥;階段Ⅱ(59～124d),因假期與疫情原因反應(yīng)器未運(yùn)行,為反應(yīng)器閑置階段;階段III(125～317d),定期向SBR1和SBR2反應(yīng)器中投加外源全程硝化污泥,其中,SBR1投加量為反應(yīng)器中污泥總量(以重量計(jì))的10%,投加周期為20d,分別在反應(yīng)運(yùn)行的第140, 160, 180, 200, 220, 240, 260, 280和300天投加;SBR2投加量為反應(yīng)器中污泥總量的2.5%,投加周期為5d,在第140～300天之間每隔5d投加1次;SBR3為空白組,不進(jìn)行投加.

1.2 試驗(yàn)水質(zhì)以及接種污泥

試驗(yàn)用水為模擬廢水,配水成分為:NH4+-N 60mg-N/L、COD(乙酸鈉) 200mg/L、MgSO4·7H2O、CaCl2·2H2O、KH2PO4及微量元素溶液Ⅰ和Ⅱ根據(jù)報(bào)道配制[14].SBR1-SBR3的接種污泥均為全程硝化和厭氧氨氧化污泥,其中全程硝化污泥取自小試規(guī)模全程硝化-反硝化SBR反應(yīng)器,厭氧氨氧化污泥取自小試規(guī)模的升流式厭氧污泥床反應(yīng)器,全程硝化污泥與厭氧氨氧化污泥的接種比例為25:1.后續(xù)生物添加污泥均取自全程硝化-反硝化SBR反應(yīng)器.

1.3 檢測(cè)項(xiàng)目

1.3.1 常規(guī)檢測(cè)項(xiàng)目 所取水樣經(jīng)0.45μm定性濾紙過(guò)濾后,按照《水和廢水監(jiān)測(cè)方法》[15]測(cè)定以下參數(shù):采用納氏試劑分光光度法測(cè)定氨氮濃度,采用麝香草酚法測(cè)定亞硝酸鹽氮濃度,采用N-(1-萘基)-乙二胺光度法測(cè)定硝酸鹽氮濃度,SV、SVI、MLSS均采用重量法測(cè)定.pH值、DO值均采用便攜式pH和DO在線監(jiān)測(cè)記錄儀(WTW,德國(guó))測(cè)定. 取約25mL混合污泥樣品進(jìn)行污泥粒徑的檢測(cè),采用激光粒度儀(Winner2308A)測(cè)定.

1.3.2 微生物最大活性檢測(cè) 在第304d(階段III)測(cè)定SBR1-SBR3中AOB、NOB和AnAOB的最大活性[16].測(cè)定AOB和NOB最大活性時(shí),取300mL泥水混合液放入500mL的錐形瓶中,先采用去離子水潤(rùn)洗3遍,再進(jìn)行測(cè)定,初始氨氮和亞硝酸鹽氮濃度分別為30和15mg-N/L,DO維持在3～4mg/L.在反應(yīng)周期的末期采用原位測(cè)定AnAOB最大活性,以避免DO和COD對(duì)AnAOB的影響,初始氨氮和亞硝酸鹽氮濃度分別為30和15mg-N/L.

1.3.3 菌群多樣性檢測(cè) 在運(yùn)行第1和317d時(shí)取反應(yīng)器中混合污泥樣品50mL,4000r/min離心后倒掉上清液,泥樣通過(guò)冷凍干燥處理后,送至美吉生物醫(yī)藥科技有限公司,采用Illumina MiSeq PE300平臺(tái)進(jìn)行和高通量測(cè)序.

2 結(jié)果與討論

2.1 脫氮性能分析

如圖2和表2所示, 在階段I(1～58d),SBR1～ SBR3均未投加全程硝化污泥.SBR1～SBR3的平均氨氮降解率分別為54.3%,48.8%和53.8%,平均出水硝酸鹽氮濃度分別為6.7,7.1和7.5mg-N/L,同時(shí), SBR1～SBR3的平均總氮去除率較低(36.5%,31.7%和35.5%).這表明,在階段I,3個(gè)反應(yīng)器的整體脫氮效果均較差,且脫氮效果波動(dòng)較大.

圖2 SBR1～SBR3脫氮性能變化規(guī)律

階段III前期(125～139d)為污泥恢復(fù)期.從第140天開(kāi)始,分別定期向SBR1和SBR2中投加全程硝化污泥,SBR3為空白組.在140～317d,SBR1～SBR3的出水氨氮濃度均逐漸下降,平均出水氨氮濃度分別由5.3,7.5和10.2mg-N/L下降至4.6,2.7和5.1mg-N/L,平均氨氮去除率分別由78.9%,75.5%和65.1%上升至84.3%,90.4%和83.6%.結(jié)果表明,SBR2的氨氮去除效果明顯優(yōu)于SBR1和SBR3.在第140～219d, SBR1～SBR3的出水硝酸鹽氮濃度分別為8.1,9.4和7.5mg-N/L,仍然處于較高的水平.階段III后期(260～ 317d),出水硝酸鹽氮濃度均逐漸下降,SBR1～SBR3的平均出水硝酸鹽氮濃度分別下降至4.6,4.1和4.2mg-N/L.與之相對(duì)應(yīng)地,SBR1～SBR3的總氮去除率逐漸增加,分別升高至67.2%,76.3%和66.3%.隨著試驗(yàn)的進(jìn)行,SBR1～SBR3的脫氮性能逐漸變好, SBR2的脫氮性能明顯優(yōu)于SBR1和SBR3,SBR1的脫氮性能略好于SBR3,此外,由圖2可看出,SBR1與SBR2的脫氮性能較為穩(wěn)定.這表明,外源全程硝化污泥對(duì)短程硝化厭氧氨氧化系統(tǒng)穩(wěn)定脫氮有一定程度的促進(jìn)作用,與前期報(bào)道結(jié)果一致,且短周期分批次投加的促進(jìn)效果更為明顯[13]

表2 SBR1-SBR3各階段脫氮性能

2.2 主要功能菌最大活性分析

為了進(jìn)一步探究外源全程硝化污泥對(duì)系統(tǒng)脫氮性能的影響機(jī)理,在階段III后期(第304 天)考察了3個(gè)反應(yīng)器中AnAOB最大活性以及AOB與NOB的最大活性比(圖3).有研究表明,AOB與NOB的活性比是啟動(dòng)和穩(wěn)定短程硝化的重要因素,可以作為短程硝化快速啟動(dòng)的一個(gè)控制條件[17].在SPNA系統(tǒng)中,AOB與NOB的活性比值越高,意味著AOB比NOB更具有生長(zhǎng)優(yōu)勢(shì),越有利于維持短程硝化效果,也更利于AnAOB競(jìng)爭(zhēng)亞硝酸鹽氮基質(zhì),最終提高系統(tǒng)脫氮性能和穩(wěn)定性[18-19].

由圖3可得,在第304d,SBR1～SBR3的AOB與NOB活性比分別為8.79,9.83和8.78.可以看出投加外源全程硝化污泥可能可提高SBR1與SBR2系統(tǒng)中AOB與NOB的活性差值,且短周期分批次投加的效果要明顯高于長(zhǎng)周期分批次投加.定期向SPNA系統(tǒng)中投加全程硝化污泥,可提高系統(tǒng)中AOB與NOB活性,但在間歇曝氣條件下,NOB活性受到明顯抑制[12],而AOB活性受到的影響較小,因此,間歇曝氣條件下投加外源全程硝化污泥,可能選擇性地強(qiáng)化了AOB活性,提高AOB與NOB的活性比,促進(jìn)短程硝化效果,進(jìn)而為AnAOB提供更多亞硝酸鹽氮,促進(jìn)厭氧氨氧化反應(yīng)和AnAOB富集,這與前期研究結(jié)果一致.同時(shí),對(duì)比SBR1和SBR2,短周期分批次投加對(duì)于系統(tǒng)而言是一種更為穩(wěn)定的投加方式,即每次只加少量的NOB對(duì)系統(tǒng)中總AOB/ NOB活性比的沖擊和影響較小,系統(tǒng)的穩(wěn)定性更強(qiáng). SBR1～SBR3中AnAOB最大活性分別由3.43mg-N/ (L·h)升高至7.66,8.19和7.31mg-N/(L·h).與不作任何投加的空白組相比,投加外源全程硝化污泥的SBR1和SBR2有更高的AnAOB活性,驗(yàn)證了上述推測(cè),且與脫氮性能變化一致.這說(shuō)明,投加外源全程硝化污泥有利于SPNA系統(tǒng)的厭氧氨氧化脫氮,且在總投加量一樣的條件下,短周期分批次投加的效果好于長(zhǎng)周期分批次投加.

圖3 AnAOB最大活性與AOB、NOB最大活性比

2.3 微生物菌群結(jié)構(gòu)分析

在第1和317d對(duì)SBR1～SBR3中微生物群落結(jié)構(gòu)進(jìn)行分析(圖4,表3).SBR1～SBR3的兩大優(yōu)勢(shì)菌門均為變形菌門(Proteobacteria)和綠彎菌門(Chloroflexi).其中,混合接種污泥中變形菌門和綠彎菌門的比例分別為34.06%和20.57%,試驗(yàn)第317天,SBR1～SBR3的變形菌門比例分別為51.09%, 54.05%和53.58%,綠彎菌門分別為13.41%,13.14%和13.70%,整體比例有所升高.有相關(guān)研究報(bào)道稱Proteobacteria和Chloroflexi與反硝化作用有關(guān)[20-22].此外,AnAOB所屬的浮霉菌門(Planctomycetota)相對(duì)豐度也在不斷增加,SBR1～SBR3的Planctomycetota豐度分別由1.43%升高至3.47%, 3.93%和3.61%.這些結(jié)果可能是試驗(yàn)后期SBR1～SBR3脫氮性能均有所提高的原因之一.

圖4 SBR1～SBR 3門水平上微生物組成

在屬水平上,SBR1～SBR3中的相對(duì)豐度分別由1.75%(1d)上升到2.58%、1.94%和2.18%(317d).表明SBR1～SBR3中NOB均有不同程度的提高,且SBR1中的NOB豐度明顯高于另外兩組,分析是因?yàn)樵囼?yàn)投加的外源全程硝化污泥有較高的NOB豐度,投加后會(huì)使系統(tǒng)的相對(duì)豐度升高.但值得注意的是,SBR2中NOB相對(duì)豐度增加幅度最小,低于空白組,表明短周期分批次投加外源全程硝化污泥不會(huì)造成SPNA系統(tǒng)中NOB豐度的額外增加,反而有一定抑制NOB生長(zhǎng)的作用.為NOB的典型菌屬,其含量越低越利于實(shí)現(xiàn)短程硝化,同時(shí)SBR1～SBR3中AOB的優(yōu)勢(shì)菌種的相對(duì)豐度分別由0.19%上升至1.6%、1.66%和1.66%.該結(jié)果與AOB和NOB活性比的變化規(guī)律一致,表明短周期分批次投加外源全程硝化污泥更有利于穩(wěn)定短程硝化效果.

在試驗(yàn)后期,為SBR1～SBR3中優(yōu)勢(shì)菌屬,SBR1～SBR3中的相對(duì)豐度由8.8%分別上升至32.75%、37.96%和36.96%,有研究指出作為一種內(nèi)源短程反硝化菌,可以將COD轉(zhuǎn)換為內(nèi)碳源,有利于亞硝酸鹽氮積累,進(jìn)而有利于促進(jìn)系統(tǒng)的厭氧氨氧化反應(yīng)的進(jìn)行[23-24].SBR2中豐度最高,短周期分批次投加全程硝化污泥可能利于促進(jìn)富集,這可能也是SBR2脫氮性能較好的原因之一.為優(yōu)勢(shì)AnAOB,其相對(duì)豐度由0.03%分別上升至0.28%、0.26%、0.32%,與AnAOB活性的變化規(guī)律有所不同,分析可能是因?yàn)楦咄繙y(cè)序數(shù)據(jù)使用的是相對(duì)豐度,定期向SBR1和SBR2添加全程污泥,全程硝化污泥中AnAOB豐度較低,而空白組未做任何生物添加,所以導(dǎo)致SBR1與SBR2的AnAOB相對(duì)豐度略低于空白組.

表3 SBR1～SBR3屬水平上微生物群落相對(duì)豐度

注:不同灰度底色代表屬水平上微生物群落相對(duì)豐度大小,底色越深,豐度越大.

2.4 粒徑分析

分別于第185和315天,對(duì)SPNA系統(tǒng)中污泥粒徑進(jìn)行檢測(cè)(圖5).結(jié)果表明SBR1的小絮體污泥(0～100μm)由55.71%增加至70.59%,SBR2由 41.26%增加至75.54%,SBR3由67.17%降低至48.71%,而SBR1中粒徑較大的活性污泥(>200μm)由13.58%降低至1.95%,SBR2由31.6%降低至2.7%,SBR3由2.59%增加至19.42%.可以得出,投加外源全程硝化污泥使得反應(yīng)器內(nèi)小絮體所占比例增高,推測(cè)原因?yàn)橥都拥耐庠慈涛勰嗔捷^小,使系統(tǒng)中的污泥粒徑整體有所下降.

有相關(guān)研究證明污泥顆粒越大,越有利于SPNA系統(tǒng)脫氮效果[25].因?yàn)殡S著粒徑的增大,相同體積的顆粒污泥的比表面積變小,污泥顆粒單位面積的氨氮負(fù)荷增加,氧的傳質(zhì)效率變低,進(jìn)而使得顆粒內(nèi)的好氧面積變小,缺氧面積變大.一方面,AOB的氧親合力大于NOB,在此條件下利于短程硝化效果的穩(wěn)定;另一方面,有利于厭氧氨氧化菌生長(zhǎng)和持留,所以大顆粒污泥在理論上更有利于AOB、AnAOB的富集和NOB的不斷淘洗,進(jìn)而有利于提高系統(tǒng)的脫氮性能[26].因此,若投加的外源全程硝化污泥的粒徑較大,可能會(huì)提高SPNA系統(tǒng)中的污泥粒徑范圍,進(jìn)一步促進(jìn)AnAOB富集,提高系統(tǒng)穩(wěn)定性.

本試驗(yàn)所用的全程硝化污泥粒徑較小,導(dǎo)致投加外源全程硝化污泥的SBR1和SBR2中粒徑范圍均顯著低于SBR3,但即便如此,SBR1和SBR2的整體脫氮效果仍明顯優(yōu)于SBR3,SBR1與SBR2中AnAOB的活性以及AOB/NOB活性比值均高于SBR3.上述結(jié)果表明,即使在粒徑較小的情況下,試驗(yàn)組的脫氮效果仍好于空白組,投加外源全程硝化污泥對(duì)系統(tǒng)運(yùn)行性能的提高效果可以彌補(bǔ)由于粒徑小對(duì)系統(tǒng)性能的影響.

圖5 SBR1-SBR3在D185和D315的粒徑分布

3 結(jié)論

3.1 向城市污水短程硝化-厭氧氨氧化系統(tǒng)中投加外源全程硝化污泥利于提高系統(tǒng)脫氮性能和穩(wěn)定性,其中,在投加總比例相同的條件下,短周期分批次投加(投加周期為5d,投加量為2.5%)全程硝化污泥效果更好.

3.2 全程硝化污泥中含有較高的AOB和NOB豐度,在間歇曝氣條件下向SPNA系統(tǒng)中投加全程硝化污泥,可選擇提高SPNA系統(tǒng)中AOB與NOB的活性比,進(jìn)而可為AnAOB提供更穩(wěn)定的亞硝酸鹽氮,促進(jìn)AnAOB富集.

3.3 短周期分批次投加外源全程硝化污泥可實(shí)現(xiàn)更高的AOB與NOB活性比值,有利于抑制NOB活性和維持穩(wěn)定的短程硝化效果,促進(jìn)厭氧氨氧化脫氮;此外,短周期分批次投加更利于富集內(nèi)源短程反硝化菌,進(jìn)一步促進(jìn)厭氧氨氧化反應(yīng)和維持系統(tǒng)穩(wěn)定.因此,不同的污泥投加方式對(duì)系統(tǒng)脫氮效果的促進(jìn)程度不同,將本研究成果應(yīng)用于其他系統(tǒng)中時(shí),可能需要對(duì)投加量與周期進(jìn)行進(jìn)一步優(yōu)化.

[1] Li W W, Sheng G P, Zeng R, et al. China's wastewater discharge standards in urbanization: evolution, challenges and implications [J]. Environmental Science and Pollution Research International, 2012, 19(5):1422-1431.

[2] 張小玲,張 萌,陳紫薇,等.內(nèi)碳源短程反硝化啟動(dòng)及EPD- ANAMMOX耦合工藝性能[J]. 中國(guó)環(huán)境科學(xué), 2022,42(2):601-611.

Zhang X L, Zhang M, Chen Z W, et al.Start-up of endogenous partial denitrification and performance of EPD-ANAMMOX coupling process [J]. China Environmental Science, 2022,42(2):601-611.

[3] Susanne L, Eva M G, Siegfried E V, et al. Full-scale partial nitritation/ anammox experiences – An application survey [J]. Water Research, 2014,55:292-303.

[4] Carmen L, Drewes J E, Liu Y, et al. Strategies for enhanced deammonification performance and reduced nitrous oxide emissions [J]. Bioresource Technology, 2017,236:174-185.

[5] Qiao S, Tian T, Duan X M, et al. Novel single-stage autotrophic nitrogen removal via co-immobilizing partial nitrifying and anammox biomass [J]. Chemical Engineering Journal, 2013,230:19-26.

[6] Duan H R, Ye L, Lu X Y, et al. Overcoming nitrite oxidizing bacteria adaptation through alternating sludge treatment with free nitrous acid and free ammonia [J]. Environmental Science & Technology, 2019, 53(4):1937-1946.

[7] Miao Y Y, Zhang L, Yu D S, et al. Application of intermittent aeration in nitrogen removal process: development, advantages and mechanisms [J]. Chemical Engineering Journal, 2022,430:133184.

[8] 周夢(mèng)雨,彭黨聰,韓 蕓,等.間歇曝氣對(duì)部分硝化-厭氧氨氧化處理氨氮廢水的影響 [J]. 中國(guó)環(huán)境科學(xué), 2022,42(3):1120-1127.

Zhou M Y, Peng D C, Han Y, et al. Partial nitrification-anaerobic ammonia oxidation for the treatment of moderately concentrated ammonia-nitrogen wastewater:Effect of intermittent aeration on nitrogen removal performance [J]. China Environmental Science, 2022,42(3):1120-1127.

[9] Liu G Q, Wang J M. Long-term low DO enriches and shifts nitrifier community in activated sludge [J]. Environmental Science & Technology, 2013,47(10):5109-5117.

[10] Wang Z B, Zhang S Z, Zhang L, et al. Restoration of real sewage partial nitritation-anammox process from nitrate accumulation using free nitrous acid treatment [J]. Bioresource Technology, 2018,251: 341-349.

[11] Karol T, Elzbieta P, Jozef T. Pilot scale studies on nitritation-anammox process for mainstream wastewater at low temperature [J]. Water Science and Technology, 2016,73(4):761-768.

[12] Li S, Chen Y P, Li C, et al. Influence of free ammonia on completely autotrophic nitrogen removal over nitrite (CANON) process [J]. Applied Biochemistry and Biotechnology, 2012,167(4):694-704.

[13] Miao Y Y, Zhang L, Li B K, et al. Enhancing ammonium oxidizing bacteria activity was key to single-stage partial nitrification-anammox system treating low-strength sewage under intermittent aeration condition [J]. Bioresource Technology, 2017,231:36-44.

[14] Zhang W K, Yu D S, Zhang J H, et al. Start-up of mainstream anammox process through inoculating nitrification sludge and anammox biofilm: Shift in nitrogen transformation and microorganisms [J]. Bioresource Technology, 2022,347:126728- 126728.

[15] 國(guó)家環(huán)境保護(hù)總局.水和廢水監(jiān)測(cè)分析方法(第四版) [M]. 第4版.北京:中國(guó)環(huán)境科學(xué)出版社, 2002:200-284.

State Environmental Protection Administration of China. Water and waste water monitoring and analysis method [M]. 4th Edition. Beijing. China Environmental Science Press, 2002:200-284.

[16] Miao Y Y, Zhang J H, Peng Y Z, et al. An improved start-up strategy for mainstream anammox process through inoculating ordinary nitrification sludge and a small amount of anammox sludge [J]. Journal of Hazardous Materials, 2020,384(C):121325.

[17] 卞 偉,李 軍,趙白航,等.硝化污泥中AOB/NOB對(duì)硝化特性的影響 [J]. 中國(guó)環(huán)境科學(xué), 2016,36(8):2395-2401.

Bian W, Li J, Zhao B H, et al. The effect of AOB/NOB in nitrifying sludge on nitrification characteristics [J]. China Environmental Science, 2016,36(8):2395-2401.

[18] 陳曉軒,劉 春,楊景亮,等.短程硝化啟動(dòng)運(yùn)行中功能菌群變化研究[J]. 微生物學(xué)通報(bào), 2012,39(5):597-605.

Chen X X, Liu C, Yang J L, et al. Variation of functional bacteria during start-up and operation of partial nitrification process [J]. Microbiology China, 2012,39(5):597-605.

[19] Wan C L, Sun S P, Lee D J, et al. Partial nitrification using aerobic granules in continuous-flow reactor: Rapid startup [J]. Bioresource Technology, 2013,142:517-522.

[20] Yao H, Zhao X C, Fan L R, et al. Pilot-scale demonstration of one-stage partial nitritation/anammox process to treat wastewater from a coal to ethylene glycol (CtEG) plant [J]. Environmental Research, 2021,208:112540-112540.

[21] Rubio-Rincón F J, Lopez-Vazquez C M, Welles L, et al. Cooperation betweenandclade I, in denitrification and phosphate removal processes [J]. Water Research, 2017,120:156-164.

[22] 常堯楓,郭萌蕾,謝軍祥,等.厭氧氨氧化脫氮除碳功能菌群結(jié)構(gòu)及代謝途徑 [J]. 中國(guó)環(huán)境科學(xué), 2022,42(3):1138-1145.

Chang Y F, Guo M L, Xie J X, et al. The structure and metabolic pathway of functional bacteria for nitrogen and carbon removal in Anammox [J]. China Environmental Science, 2022,42(3):1138-1145.

[23] Ji J T, Peng Y Z, Wang B, et al. Achievement of high nitrite accumulation via endogenous partial denitrification (EPD) [J]. Bioresource Technology, 2017,224:140-146.

[24] Cui H H, Zhang L, Zhang Q, et al. Advanced nitrogen removal from low C/N municipal wastewater by combining partial nitrification- anammox and endogenous partial denitrification-anammox (PN/A- EPD/A) process in a single-stage reactor [J]. Bioresource Technology, 2021,339:125501-125501.

[25] 易名儒,曾 玉,劉 永,等.不同粒徑好氧顆粒污泥的結(jié)構(gòu)穩(wěn)定性及污染物去除效果 [J]. 環(huán)境科技, 2021,34(5):23-28.

Yi M R, Zeng Y, Liu Y, et al. Structural Stability and Contaminant Removal Efficiency of Aerobic Granular Sludge with Different Particle Size [J]. Environmental Science and Technology, 2021,34(5): 23-28.

[26] 梁東博,卞 偉,王文嘯,等.低溫條件下好氧顆粒污泥培養(yǎng)及其脫氮性能研究 [J]. 中國(guó)環(huán)境科學(xué), 2019,39(2):634-640.

Liang D B, Bian W, Wang W X, et al. Aerobic granular sludge formation and nutrients removal characteristics under low temperature [J]. China Environmental Science, 2019,39(2):634-640.

Effects of exogenous nitrification sludge on the single-stage partial nitrification-anammox system of municipal sewage.

HE Zhao-ming1, LIU Jia-ni1,TIAN Ya-ru1, YU De-shuang1, MIAO Yuan-yuan1*, ZHANG Wen-ke1, MA Guo-cheng1, ZHAO Xin-chao1, YUAN Yue2

(1.Department of Environment Science and Engineering, Qingdao University, Qingdao 266071, China；2.Shanghai Municipal Engineering Design and Research Institute Co. Ltd, Shanghai 200092, China)., 2022,42(9)：4122～4128

In order to improve the nitrogen removal performance and stability of the single-stage partial nitrification-anammox (SPNA) system treating municipal sewage, the effects and mechanisms of adding exogenous nitrification sludge to mainstream SPNA system were evaluated under intermittent aeration condition. The results showed that the total nitrogen removal efficiency of the control SPNA system (SBR3) increased from 35.5% to 66.3%. The total nitrogen removal efficiencies of SPNA systems with nitrification sludge added in batches in a short cycle (SBR2, the dosing period was 5d, the dosing ratio was 2.5%) and in batches in a long cycle (SBR1, the dosing period was 5d, the dosing ratio was 2.5%) increased from 31.7% and 36.5% to 76.3% and 67.2%, respectively. And the addition of nitrification sludge was beneficial to the nitrogen removal performance of mainstream SPNA system and adding nitrification sludge in batches in a short cycle showed better performance. The maximum activities of anaerobic ammonium oxidation bacteria (AnAOB) in SBR1-SBR3 increased from 3.43mg-N/(L·h) to 7.66, 8.19% and 7.31mg-N/(L·h), respectively, and the activity ratios of ammonia oxidizing bacteria (AOB) and nitrite oxidizing bacteria (NOB) were 8.79, 9.83 and 8.78, respectively. Adding nitrification sludge under intermittent aeration condition could selectively inhibit NOB and enrich AOB, leading to a higher activity ratio of AOB and NOB and more stable partial nitrification, which provided stable substrates for AnAOB. In addition, adding the nitrification sludge in batches in a short cycle could reduce the impact of NOB of exogenous nitrification sludge on the system, which was more conducive to achieve high AOB/NOB activity ratio and improved the stability of system. Moreover, the relative abundance of, thought to be the endogenous partial denitrification bacteria, increased obviously, providing AnAOB with more nitrite and was further beneficial to AnAOB enrichment. Therefore, this study provided new ideas for promoting the application of mainstream anammox process.

single-stage of partial nitrification-anammox；bioaugmentation；nitrification sludge；intermittent aeration；high- throughput sequencing；influencing factors

X703

A

1000-6923(2022)09-4122-07

2022-02-28

國(guó)家自然科學(xué)基金資助項(xiàng)目(51978348),青島市科技計(jì)劃項(xiàng)目科技惠民示范引導(dǎo)專項(xiàng)(2022-3-7-cspz-11-nsh),山東省大學(xué)生創(chuàng)新創(chuàng)業(yè)計(jì)劃(S202011065123),上海市青年科技英才揚(yáng)帆計(jì)劃資助(20YF1445600)

*責(zé)任作者, 講師, Miaoyy@qdu.edu

賀昭銘(2000-),女,山東棗莊人,青島大學(xué)本科生,環(huán)境工程專業(yè).