象山港大黃魚Pseudosciaena crocea網(wǎng)箱養(yǎng)殖區(qū)沉積物-水界面營(yíng)養(yǎng)鹽通量研究

廖紅芳，鄭忠明，REGAN Nicholaus，朱津永

(1.寧波大學(xué) 海洋學(xué)院，浙江 寧波 315211; 2.臨武一中， 湖南 郴州 424300; 3. 浙江海洋高效健康養(yǎng)殖協(xié)同

創(chuàng)新中心，浙江 寧波 315211)

?

象山港大黃魚Pseudosciaenacrocea網(wǎng)箱養(yǎng)殖區(qū)沉積物-水界面營(yíng)養(yǎng)鹽通量研究

廖紅芳1,2,3，鄭忠明*1,3，REGAN Nicholaus1,3，朱津永1,3

(1.寧波大學(xué) 海洋學(xué)院，浙江 寧波 315211; 2.臨武一中， 湖南 郴州 424300; 3. 浙江海洋高效健康養(yǎng)殖協(xié)同

創(chuàng)新中心，浙江 寧波 315211)

摘要:2013年5月、8月和11月調(diào)查了象山港大黃魚網(wǎng)箱養(yǎng)殖區(qū)及附近沉積物中總有機(jī)氮(TON)、總有機(jī)碳(TOC)和總磷(TP)含量，并采用實(shí)驗(yàn)室模擬法研究了底泥耗氧率(SOCs)和沉積物-水界面營(yíng)養(yǎng)鹽和)通量。結(jié)果表明：養(yǎng)殖區(qū)(YZ)沉積物中的TON和TP含量顯著高于距離養(yǎng)殖區(qū)50 m(F1)和100 m(F2)的區(qū)域(P<0.05)。底泥釋放到上覆水中，但是從上覆水中吸收和。沉積物-水界面營(yíng)養(yǎng)鹽通量表現(xiàn)出明顯的季節(jié)性變化，在8月，及的釋放量達(dá)到最大值。上覆水中和的質(zhì)量濃度隨著沉積物-水界面營(yíng)養(yǎng)鹽通量的變化而變化。研究表明，象山港大黃魚養(yǎng)殖活動(dòng)對(duì)養(yǎng)殖區(qū)底泥造成了一定污染，且通過(guò)影響沉積物-水界面營(yíng)養(yǎng)鹽通量影響上覆水中營(yíng)養(yǎng)鹽分布，最終給整個(gè)養(yǎng)殖系統(tǒng)造成生態(tài)負(fù)擔(dān)。

關(guān)鍵詞:養(yǎng)殖；大黃魚；底泥；營(yíng)養(yǎng)鹽通量；象山港

0引言

網(wǎng)箱養(yǎng)殖在過(guò)去20 a迅速發(fā)展，是全球水產(chǎn)養(yǎng)殖業(yè)中增長(zhǎng)最快的產(chǎn)業(yè)之一。然而在其迅速擴(kuò)增的同時(shí)，對(duì)周邊環(huán)境也造成了一定的困擾。網(wǎng)箱養(yǎng)殖對(duì)周邊環(huán)境的影響主要是產(chǎn)生殘餌、排泄物等有機(jī)廢物[1-2]，它們絕大部分以顆粒態(tài)形式沉積到底泥中，使沉積物質(zhì)量迅速惡化[3]。積累到底泥中的有機(jī)物經(jīng)過(guò)一系列的生物地球化學(xué)作用，最終以氮、磷等可溶性營(yíng)養(yǎng)鹽形式釋放到水中，可能造成水體富營(yíng)養(yǎng)化[4]。被污染的沉積物成為潛在污染源，反過(guò)來(lái)影響整個(gè)水產(chǎn)養(yǎng)殖系統(tǒng)甚至還會(huì)威脅野生生物和人類的健康[5-6]。近幾年，越來(lái)越多的人關(guān)注網(wǎng)箱養(yǎng)殖對(duì)沉積環(huán)境造成的影響[7-8]。養(yǎng)殖對(duì)沉積環(huán)境的影響與漁場(chǎng)地點(diǎn)、養(yǎng)殖種類、投喂飼料、養(yǎng)殖規(guī)模及周圍生物區(qū)系對(duì)固體廢棄物的吸收能力等有關(guān)[9-10]。

大黃魚是重要的經(jīng)濟(jì)魚類，在我國(guó)廣泛養(yǎng)殖。象山港內(nèi)灣西瀘港是大黃魚的主要養(yǎng)殖基地之一，總面積約52 km2，水深為10～20 m。象山西瀘港口小港大，其頸門最窄處寬僅為1 km左右，水體交換能力弱。近幾年網(wǎng)箱數(shù)量成倍增長(zhǎng)，養(yǎng)殖區(qū)域環(huán)境問(wèn)題日益凸顯，養(yǎng)殖活動(dòng)對(duì)周圍環(huán)境造成的影響逐漸引起人們的關(guān)注[11-12]。但是目前關(guān)于大黃魚網(wǎng)箱養(yǎng)殖對(duì)沉積環(huán)境的影響了解較少。本文通過(guò)測(cè)定沉積層中氮、磷等有機(jī)物含量及沉積物-水界面營(yíng)養(yǎng)鹽通量，調(diào)查大黃魚網(wǎng)箱養(yǎng)殖對(duì)沉積環(huán)境及整個(gè)水域生態(tài)系統(tǒng)的影響，以期對(duì)水產(chǎn)養(yǎng)殖業(yè)可持續(xù)發(fā)展戰(zhàn)略制定及整個(gè)海岸區(qū)域的管理提供科學(xué)支持。

1方法

1.1研究地點(diǎn)及樣品采集

分別于2013年5月、8月和11月在象山西瀘港生態(tài)養(yǎng)殖基地大黃魚養(yǎng)殖區(qū) (29°32′0.16″N，121°45′4.09″E)采集樣品。有3個(gè)采樣點(diǎn)：大黃魚養(yǎng)殖區(qū)(YZ)、距離大黃魚網(wǎng)箱養(yǎng)殖區(qū)50 m(F1)及100 m(F2)區(qū)域(圖1)，每個(gè)地點(diǎn)隨機(jī)采3個(gè)樣品。

圖1　采樣站點(diǎn)示意圖Fig.1　Sketch map of sample sites

用無(wú)擾動(dòng)沉積物采樣器[13]采集沉積物。迅速將采集的樣品用沉積物轉(zhuǎn)移裝置(圖2)轉(zhuǎn)移至直徑與采樣管一樣的培養(yǎng)管中，使培養(yǎng)管中的泥深為20 cm左右，注意避免沉積物擾動(dòng)。培養(yǎng)管底部用塑料薄膜密封，頂端蓋上橡膠蓋。立即將采好的泥樣避光冷凍保存，以抑制底棲生物和微生物活動(dòng)，從而降低生物影響。用采水器采集水樣。用YSI Proplus 型多參數(shù)測(cè)量?jī)x現(xiàn)場(chǎng)測(cè)定水溫及水中溶解氧。樣品采好后在1 h內(nèi)帶回實(shí)驗(yàn)室。

圖2　沉積物轉(zhuǎn)移裝置示意圖Fig.2　Sketch map of sediment transfer device

1.2實(shí)驗(yàn)室模擬實(shí)驗(yàn)

圖3　沉積物培養(yǎng)裝置示意圖Fig.3　Sketch map of benthic chamber specially designedand built for the present study

1.3參數(shù)測(cè)定及分析方法

(1)

式中：F表示營(yíng)養(yǎng)鹽通量或底泥耗氧率；ΔC表示培養(yǎng)前后營(yíng)養(yǎng)鹽或氧質(zhì)量濃度的變化(同時(shí)用空白對(duì)照校正)；V表示培養(yǎng)管中上覆水的體積；A表示培養(yǎng)管底部的橫截面積；t表示培養(yǎng)時(shí)間。F為正則表示沉積物向水中釋放出營(yíng)養(yǎng)物質(zhì)，為負(fù)則表示營(yíng)養(yǎng)鹽進(jìn)入沉積物中。

用元素分析儀 vario EL cube測(cè)定沉積物中總有機(jī)氮(TON)、總有機(jī)碳(TOC)及硫化物的含量；TON和TOC測(cè)定之前采用氣相法酸化，將沉積物放入盛有濃鹽酸的干燥器中過(guò)夜，然后在烘箱(60 ℃)中烘干，除去過(guò)量的鹽酸。參照MUDROCH et al[15]的方法測(cè)定沉積物中的總磷(TP)。 采用燒失重法測(cè)定沉積物中有機(jī)物(OM)含量，稱取一定量濕沉積物，在105 ℃下烘4 h，將烘干的沉積物在550 ℃下馬弗爐中燒5 h，前后損失的質(zhì)量與原有干沉積物質(zhì)量的比值為L(zhǎng)OI(Loss-on-Ignition)，即沉積物中OM含量[16]。

1.4數(shù)據(jù)分析

采用SPSS 17.0分析數(shù)據(jù)。沉積物中的TP、TON

和 TOC含量及沉積物-水界面營(yíng)養(yǎng)鹽通量先進(jìn)行單因素方差分析(ANOVA)，然后用Duncan法進(jìn)行多重比較。方差分析前先檢驗(yàn)方差齊性。顯著性的臨界值為0.05。百分比數(shù)據(jù)(包括TOC、TON和TP含量)先通過(guò)反正弦轉(zhuǎn)換后再進(jìn)行統(tǒng)計(jì)分析。用Origin 8.0 作圖。

2結(jié)果

2.1底泥理化性質(zhì)

3次采樣中，YZ區(qū)沉積物(1～20 cm)有較強(qiáng)的魚腥臭味，除8月采集樣品的8～20 cm層為灰褐色外，沉積物物理特征類似，均為深灰色，夾雜著黑色團(tuán)塊。F1和F2區(qū)的沉積物(1～20 cm)略帶魚腥味，為灰褐色。

圖4　2013年5月、8月和11月養(yǎng)殖區(qū)(YZ)、50 m區(qū)(F1)和100 m區(qū)(F2)沉積物中總磷含量Fig.4　Values of total phosphorous in sediments for the fish farm (YZ), the stations 50 m away (F1) and 100 m away (F2)in May 2013, Aug. 2013 and Nov. 2013誤差棒為標(biāo)準(zhǔn)差(n=3)Error bars indicate standard deviations (n=3)

圖5　2013年5月、8月和11月養(yǎng)殖區(qū)(YZ)、50 m區(qū)(F1)和100 m區(qū)(F2)沉積物中總有機(jī)碳(a)和總有機(jī)氮(b)含量Fig.5　Values of total organic carbon (a) and total organic nitrogen (b) in sediments for the fish farm (FZ), the stations 50 maway (Y1) and 100 m away (Y2) in May 2013, Aug. 2013 and Nov. 2013誤差棒為標(biāo)準(zhǔn)差(n=3)Error bars indicate standard deviations (n=3)

YZ區(qū)沉積物中TP(圖4)、TON和TOC含量(圖5)的變化范圍分別為21.625～40.125 μmol/g、0.049%～0.097%和0.504%～0.814%，而F1區(qū)和F2區(qū)沉積物中相應(yīng)有機(jī)質(zhì)的含量分別為 19.200～25.083 μmol/g、0.051%～0.069%和0.493%～0.798%。水平分布上，YZ區(qū)沉積物中的TP 和 TON含量顯著高于F1和F2區(qū)(P<0.05)；YZ區(qū)表層沉積物(0～4 cm)中的TOC含量高于F2區(qū)，但是只有8月份時(shí)有顯著性差異(P<0.05)。從季節(jié)性變化來(lái)看，YZ區(qū)表層沉積物(0～4 cm 層)中，TP含量8月最高，5月最低；TON和TOC含量由高到低依次為11月>5月>8月。沉積物中有機(jī)物(OM)的變化范圍是1.55%～2.35%，平均為1.95%(表1)。除11月外，YZ區(qū)沉積物中有機(jī)物含量高于F1和F2區(qū)，5月時(shí)與F2區(qū)差異顯著(P<0.05)。沉積物中硫化物的含量為0.17%～0.48%，各站位間差異不顯著(P>0.05)，說(shuō)明F1和F2區(qū)與YZ區(qū)站位沉積物的氧化還原條件基本相似。

表1　養(yǎng)殖區(qū)(YZ)、50 m區(qū)(F1)和100 m區(qū)(F2)沉積物中有機(jī)物(OM)和硫化物(S)含量

2.2采樣區(qū)海水水質(zhì)參數(shù)

表2　養(yǎng)殖區(qū)(YZ)、50 m區(qū)(F1)和100 m區(qū)(F2)海水溫度及水中溶解氧和營(yíng)養(yǎng)鹽質(zhì)量濃度

2.3底泥耗氧率(SOCs)及營(yíng)養(yǎng)鹽通量

YZ區(qū)底泥耗氧率(SOCs)除5月外，均高于F1和F2區(qū) (圖6)。8月，YZ區(qū)SOCs與F1區(qū)差異顯著(P<0.05),而11月則與F2區(qū)有顯著性差異(P<0.05)。YZ區(qū)在8月耗氧量最高，5月最低。

圖6　2013年5月、8月和11月養(yǎng)殖區(qū)(YZ)、50 m區(qū)(F1)和100 m區(qū)(F2)底泥耗氧率(SOCs)Fig.6　Sediment oxygen consumption (SOCs) rates for thefish farm (YZ), the stations 50 m away (F1) and 100 maway (F2) in May 2013, Aug. 2013 and Nov. 2013誤差棒表示標(biāo)準(zhǔn)差(n=3)。字母a和b表示不同地點(diǎn)差異顯著，為同一字母則無(wú)顯著性差異 (P<0.05)Error bars indicate standard deviations (n=3). Letters a and bindicate that there are notable differences in different sites, thesame letter means no notable differences (P<0.05)

3討論

3.1底泥理化性質(zhì)

圖7　2013年5月、8月和11月養(yǎng)殖區(qū)(YZ)、50 m區(qū)(F1)和100 m區(qū)(F2)沉積物-水界面和通量Fig.7　Benthic fluxes of (a), (b), (c) for the fish farm (YZ), the stations 50 m away (F1)and 100 m away (F2) in May 2013, Aug. 2013 and Nov. 2013

已有研究顯示，養(yǎng)殖活動(dòng)能導(dǎo)致沉積物的有機(jī)污染[11,15 ]。沉積層有機(jī)物的積累很可能引起水體富營(yíng)養(yǎng)化[5]，當(dāng)?shù)啄嘀杏袡C(jī)物的含量達(dá)到9%時(shí)，甚至?xí)档偷讞锶郝涞亩鄻有訹17]。本研究中，YZ區(qū)表層沉積物中的TP和TON含量顯著高于F1和F2區(qū)，表明大黃魚養(yǎng)殖活動(dòng)導(dǎo)致了沉積物中有機(jī)物的積累。養(yǎng)殖活動(dòng)對(duì)沉積環(huán)境影響的大小及范圍常因地點(diǎn)而異[10,18]。CRANFORD et al[18]和YOKOYAMA et al[8]研究指出養(yǎng)殖活動(dòng)能影響周圍300 m的區(qū)域。本實(shí)驗(yàn)中，養(yǎng)殖區(qū)周圍區(qū)域(F1和F2區(qū))沉積物中的TON(0.051%～0.069%)、TOC含量(0.493%～0.798%)與其他養(yǎng)殖區(qū)沉積物中的有機(jī)物含量差不多(表3)，表現(xiàn)出了有機(jī)物富集的趨勢(shì)，表明大黃魚養(yǎng)殖活動(dòng)對(duì)養(yǎng)殖區(qū)周圍100 m區(qū)域的沉積物造成了有機(jī)污染。本研究區(qū)域沉積物中有機(jī)物含量顯著低于菲律賓波里納奧刺目魚養(yǎng)殖區(qū)[7](表 3)，這可能與養(yǎng)殖種類和養(yǎng)殖區(qū)域水文條件(本研究區(qū)為典型的半日潮)有關(guān)。研究發(fā)現(xiàn)，本研究區(qū)域沉積物中的TON和TOC含量與東海赤潮高發(fā)區(qū)表層沉積物中TON(0.047%～0.110%)和TOC(0.32%～0.82%)含量差不多[19]，暗示大黃魚養(yǎng)殖活動(dòng)造成的有機(jī)污染可能會(huì)引起養(yǎng)殖水域水體富營(yíng)養(yǎng)化。

表3　各養(yǎng)殖區(qū)表層沉積物中TON、TOC和TP含量比較

注：空白處表示無(wú)數(shù)據(jù)

3.2沉積物-水界面營(yíng)養(yǎng)鹽通量

沉積物中氧氣的消耗過(guò)程由微生物介導(dǎo)的有機(jī)物氧化及營(yíng)養(yǎng)鹽的還原所驅(qū)使[24]。本研究中，養(yǎng)殖區(qū)的耗氧量表現(xiàn)為8月最大，除了受溫度影響外，沉積層中有機(jī)物的供給速率及有機(jī)物含量的增加是底泥耗氧量增多的一個(gè)很重要的因素[25]。有機(jī)物堆積在沉積物中，促使分解有機(jī)物的微生物群落迅速增長(zhǎng),導(dǎo)致沉積層中的耗氧大大增加[26]，這可能使底泥形成亞氧化層甚至形成無(wú)氧區(qū)域，最終影響底部營(yíng)養(yǎng)鹽的再生。本實(shí)驗(yàn)中YZ區(qū)的SOCs顯著高于F1和F2區(qū)，在其他受養(yǎng)殖活動(dòng)影響的區(qū)域也觀察到了這種現(xiàn)象[11]。

表4　各養(yǎng)殖區(qū)沉積物-水界面營(yíng)養(yǎng)鹽通量比較

注：空白處表示無(wú)數(shù)據(jù)

本實(shí)驗(yàn)中各營(yíng)養(yǎng)鹽通量表現(xiàn)出明顯的季節(jié)性變化，養(yǎng)殖區(qū)的通量在8月達(dá)到最值，可能是8月養(yǎng)殖活動(dòng)強(qiáng)度較大，產(chǎn)生的殘餌、糞便等有機(jī)物較多，促使微生物大量繁殖，加速了各種反應(yīng)；8月溫度較高，促進(jìn)了離子的擴(kuò)散，也是8月通量值達(dá)到最值的原因之一。

4小結(jié)

參考文獻(xiàn)(References)：

[1] BROOKS K M, MAHNKEN C V. Interactions of Atlantic salmon in the Pacific northwest environment: II Organic wastes [J]. Fisheries Research,2003,62(3):255-293.

[2] GRIGORAKIS K, RIGOS G. Aquaculture effects on environmental and public welfare-the case of Mediterranean mariculture [J]. Chemosphere,2011,85(6):899-919.

[3] KARAKASSIS I, TSAPAKIS M, HATZIYANNI E, et al. Impact of cage farming of fish on the seabed in three Mediterranean coastal areas [J]. ICES J Mar Sci: Journal du Conseil,2000,57(5):1 462-1 471.

[4] JIANG Zeng-jie, FANG Jian-guang, MAO Yu-ze, et al. Eutrophication assessment and bioremediation strategy in a marine fish cage culture area in Nansha Bay [J]. China Journal of Applied Phycology,2010,22(4):421-426.

[5] HUUSKONEN S E, RISTOLA T E, TUVIKENE A, et al. Comparison of two bioassays a fish liver cell line (PLHC-1) and a midge (Chironomusriparius), in monitoring freshwater sediments [J].Aquatic Toxicology,1998,44(1):47-67.

[6] HALLARE A V, SEILER T B, HOLLERT H. The versatile changing and advancing roles of fish in sediment toxicity assessment—a review [J]. Journal of Soils and Sediments,2011,11(1):141-173.

[7] HOLMER M, MARBA N, TERRADOS J, et al. Impacts of milkfish (Chanoschanos) aquaculture on carbon and nutrient fluxes in the Bolinao area Philippines [J]. Mar Pollut Bull,2002,44(7):685-696.

[8] YOKOYAMA H, ABO K, ISHIHI Y. Quantifying aquaculture-derived organic matter in the sediment in and around a coastal fish farm using stable carbon and nitrogen isotope ratios [J]. Aquaculture,2006,254(1):411-425.

[9] LAM K S, MACKAY D W, LAU T C, et al. Impact of marine fish farming on water quality and bottom sediment: a case study in the sub-tropical environment [J]. Marine Environmental Research,1994,38(2):115-145.

[10] MORATA T, SOSPEDRA J, FALCO S, et al. Exchange of nutrients and oxygen across the sediment-water interface below aSparusauratamarine fish farm in the north-western Mediterranean Sea [J]. Journal of Soils and Sediments,2012,12(10)1 623-1 632.

[11] CAI Hui-wen, SUN Ying-lan, ZHANG Xue-qing. Environmental impact of cage aquaculture and aquaculture environmental capacity in Xiangshan harbor [J]. Techniques and Equipment for Environmental Pollution Control,2006,7(11):71-76.

蔡惠文,孫英蘭,張學(xué)慶.象山港網(wǎng)箱養(yǎng)殖對(duì)海域環(huán)境的影響及其養(yǎng)殖環(huán)境容量研究[J].環(huán)境污染治理技術(shù)與設(shè)備,2006,7(11):71-76.

[12] QIU Qiong-fen, ZHANG De-min, YE Xian-sen, et al. The bacterial community of coastal sediments influenced by cage culture in Xiangshan Bay, Zhejiang, China[J]. Acta Ecologica Sinica,2013,33(2):483-491.

裘瓊芬,張德民,葉仙森，等.象山港網(wǎng)箱養(yǎng)殖對(duì)近海沉積物細(xì)菌群落的影響[J].生態(tài)學(xué)報(bào),2013,33(2):483-491.

[13] WANG You-shao, XU Ji-rong. A borderless disturbed sediment core sampler: China, CN1683915A[P].2004-10-19.

王友紹,徐繼榮.一種無(wú)邊界擾動(dòng)的單管沉積物采樣器：中國(guó)，CN1683915A[P].2004-10-19.

[14] ZHENG Zhong-ming, DONG Shuang-lin, TIAN Xiang-lin, et al. Sediment-water fluxes of nutrients and dissolved organic carbon in extensive sea cucumber culture ponds [J].Clean-Soil, Air, Water,2009,37(3):218-224.

[15] MUDROCH A, AZCUE J M, MUDROCH P. Manual of physico-chemical analysis of aquatic sediments[M]. Florida,USA: CRC Press,1995:123-124.

[16] BOYLE J. A comparison of two methods for estimating the organic matter content of sediments [J]. Journal of Paleolimnology,2004,31(1):125-127.

[17] CHICILEV S, IVANOV M. Response of the Arctic benthic community to excessive amounts of nontoxic organic matter [J]. Mar Pollut Bull,1997,35(7):280-286.

[18] CRANFORD P J, HARGRAVE B T, DOUCETTE L I. Benthic organic enrichment from suspended mussel (Mytilus edulis) culture in Prince Edward Island Canada [J]. Aquaculture,2009,292(3):189-196.

[19] WANG Li-sha, SHI Xiao-yong, ZHANG Chuan-song. Distribution and origins of organic carbon and organic nitrogen in ECS sediments of high-frequency HABs areas[J]. Marine Environmental Science,2010,29(2):165-169.

王麗莎,石曉勇,張傳松.東海赤潮高發(fā)區(qū)沉積物中有機(jī)碳,有機(jī)氮的分布及其來(lái)源[J].海洋環(huán)境科學(xué),2010,29(2):165-169.

[20] ZHANG Xue-lei, ZHU Ming-yuan, TANG Ting-yao, et al. Fluxes of nutrients at sediment-water in Sanggou Bay and Jiaozhou Bay in summer [J]. Marine Environmental Science,2004,23(1):1-4.

張學(xué)雷,朱明遠(yuǎn),湯庭耀,等.桑溝灣和膠州灣夏季的沉積物-水界面營(yíng)養(yǎng)鹽通量研究[J].海洋環(huán)境科學(xué),2004,23(1):1-4.

[21] ZHAI Bing. Distribution characteristics, influential factors and pollution sssessment of nitrogen and phosphorus in surface sediments of Xiangshan Bay[D]. Qingdao: Ocean University of China,2006.

翟濱.象山港表層沉積物中氮和磷的分布特征,影響因素及其污染評(píng)價(jià)[D].青島：中國(guó)海洋大學(xué),2006.

[22] DE VITTOR C, FAGANELI J, EMILI A, et al. Benthic fluxes of oxygen, carbon and nutrients in the Marano and Grado Lagoon (northern Adriatic Sea Italy) [J]. Estuarine Coastal and Shelf Science,2012,113:57-70.

[23] MANTZAVRAKOS E, KORNAROS M, LYBERATOS G, et al. Impacts of a marine fish farm in Argolikos Gulf (Greece) on the water column and the sediment [J]. Desalination,2007,210:110-124.

[24] J J?RGENSEN B B. Processes at the sediment-water interface[M]//BERT B, COOK R B. The major biogeochemical cycles and their interactions. SCOPE 21, Stockholm,1983:477-509.

[25] JENSEN M H, LOMSTEIN E, S?RENSEN J. Benthic NH4and NO3flux following sedimentation of a spring phytoplankton bloom in Aarhus Bight Denmark Mar [J]. Ecol Prog Ser,1990,61:87-96.

[26] AXLER R, TIKKANEN C, MCDONALD M, et al. Water quality issues associated with aquaculture: A case study in mine pit lakes [J]. Water Environ Res,1996,68(6):995-1 011.

[28] SUN San, LI Jia-hui, JIN Yang, et al. Distribution features of nutrients and flux between the sediment and water interface in Sishili bay[J].Marine Environmental Sicence,2012,31(2):195-200.

孫珊,李佳蕙,靳洋,等.煙臺(tái)四十里灣海域營(yíng)養(yǎng)鹽和沉積物-水界面交換通量[J].海洋環(huán)境科學(xué),2012,31(2):195-200.

[29] CANFIELD D E, J?GENSEN B B, FOSSING H, et al. Pathways of organic carbon oxidation in three continental margin sediments[J]. Marine Geology,1993,113(1-2):27-40.

[30] CLINE J D, RICHARDS F A. Oxygen deficient conditions and nitrate reduction in the eastern tropical North Pacific Ocean [J]. Limnol Oceanogr,1972,17(6):885-900.

[31] MURRAY J W, CODISPOTI L A, FRIEDERICH G E. Oxidation-reduction environments: the suboxic zone in the Black Sea [J]. ACS Advances in Chemistry Series,1995,244:157-176.

[32] BOON P I, MORIARTY D J W, SAFFIGNA P G. Rates of ammonium turnover and the role of amino-acid deamination in seagrass (Zosteracapricorni) beds of Moreton Bay Australia [J]. Marine Biology,1986,91(2):259-268.

[33] GARDNER W S, MCCARTHY M J, AN S. Nitrogen fixation and dissimilatory nitrate reduction to ammonium (DNRA) support nitrogen dynamics in Texas estuaries [J]. Limnology and Oceanography,2006,51(1):558-568.

Study on nutrient fluxes of sediment-water interface in cage culture zone of large yellow croakerPseudosciaenacroceain Xiangshan Bay

LIAO Hong-fang1,2,3, ZHENG Zhong-ming*1,3, REGAN Nicholaus1,3, ZHU Jin-yong1,3

(1.SchoolofMarineSciences,NingboUniversity,Ningbo315211,China；2.TheFirstMiddleSchoolofLinwu,Chenzhou424300,China; 3.CollaborativeInnovationCenterforZhejiangMarineHigh-efficiencyandHealthyAquaculture,Ningbo315211,China)

Abstract:Undisturbed sediment samples were collected from the cage culture zone and nearby of large yellow croaker’ farm in Xiangshan Bay in May, Aug. and Nov. of 2013. Total organic nitrogen (TON), total organic carbon (TOC) and total phosphorus (TP) in the sediments were determined. A simulated experiment was conducted to study the sediment oxygen consumption (SOCs) rates and ) fluxes between water column and sediments. TON and TP values of sediment in cage-zone(YZ) are generally significantly higher than those in stations of 50 m away (F1) and 100 m away (F2) (P<0.05). The sediments release to the overlying water where as they takes up and . Benthic fluxes show that intensive seasonal variations and the release of and reach peak values in August, which response to increased organic input due to the yellow croaker farming. The nutrient concentration in water changes with benthic nutrient fluxes among seasons. The results obtained in this study imply that the ongoing aquaculture activities have led to sediment organic pollution at certain extent and the polluted sediment could affect the benthic nutrient fluxes, which might cause the redistribution of nutrients in water column.

Key words:fish farming; yellow croaker; sediment; nutrient flux; Xiangshan Bay

Doi:10.3969/j.issn.1001-909X.2016.01.011

中圖分類號(hào):S967.3

文獻(xiàn)標(biāo)識(shí)碼:A

文章編號(hào):1001-909X(2016)01-0084-09

作者簡(jiǎn)介:廖紅芳(1988-)，女，湖南郴州市人，主要從事近海養(yǎng)殖水域生態(tài)方面的研究。E-mail：nicelhf@163.com*通訊作者:鄭忠明(1965-)，男，教授，主要從事水域生態(tài)學(xué)方面的研究。E-mail：zhengzhongming@nbu.edu.cn

基金項(xiàng)目:國(guó)家科技支撐計(jì)劃項(xiàng)目資助(2011BAD13B08)；國(guó)家星火計(jì)劃項(xiàng)目資助(2013GA701020)；寧波自然科學(xué)基金項(xiàng)目資助(2012A610168)

收稿日期:2014-11-05修回日期:2015-12-08

廖紅芳，鄭忠明，REGAN Nicholaus，等.象山港大黃魚Pseudosciaenacrocea網(wǎng)箱養(yǎng)殖區(qū)沉積物-水界面營(yíng)養(yǎng)鹽通量研究[J].海洋學(xué)研究,2016,34(1):84-92,doi:10.3969/j.issn.1001-909X.2016.01.011.

LIAO Hong-fang, ZHENG Zhong-ming, REGAN Nicholaus, et al. Study on nutrient fluxes of sediment-water interface in cage culture zone of large yellow croakerPseudosciaenacroceain Xiangshan Bay[J]. Journal of Marine Sciences, 2016,34(1):84-92, doi:10.3969/j.issn.1001-909X.2016.01.011.