海草床沉積物有機碳研究綜述

葉嘉暉, 邱崇玉, 曾文軒, 史云峰, 趙牧秋, 韓秋影

海草床沉積物有機碳研究綜述

葉嘉暉, 邱崇玉, 曾文軒, 史云峰, 趙牧秋, 韓秋影

(海南熱帶海洋學院崖州灣創(chuàng)新研究院, 熱帶海洋生物資源利用與保護教育部重點實驗室, 海南省近岸海洋生態(tài)環(huán)境過程與碳匯重點實驗室, 海南 三亞 572022)

海草床具有重要的生態(tài)系統(tǒng)服務功能, 可以為海洋生物提供棲息地和食物來源, 同時還具有重要的碳儲存功能, 海草床“藍碳”功能日益受到學術界的重視, 據(jù)研究全球每年海草床的碳埋藏量高達(2.7～4.4)×107MgC。近年來, 由于人類活動的影響, 世界范圍內海草床衰退嚴重, 導致海草床沉積物有機碳儲量降低。本文綜述了全球海草床沉積物有機碳的來源、組分、儲量以及指示作用; 從物理、化學和生物三方面討論了影響海草床碳儲量的環(huán)境因素。最后提出了未來主要研究方向, 主要包括加強海草床碳通量普查, 分析全球氣候變化背景下海草床沉積物有機碳的變化機制, 明確海草床碳儲量流失速率, 研究海岸帶工程對海草床沉積物有機碳的影響。評估海草床沉積物有機碳儲量及變化機制可以為全球海洋藍碳研究提供科學依據(jù)。

海草床; 沉積物有機碳; 來源; 儲量; 環(huán)境因素

海草通常生活在潮間帶和潮下帶的淺水區(qū)域, 是一種廣泛分布于熱帶以及溫帶海域的沉水性被子植物[1]。印度-太平洋區(qū)、熱帶大西洋區(qū)、溫帶北大西洋區(qū)、溫帶北太平洋區(qū)、溫帶南大洋區(qū)和地中海區(qū)為全球6個主要海草分布區(qū)[1], 共有6科72種海草[2]。熱帶地區(qū)海草種類較多[1], 熱帶印度-太平洋地區(qū)的海草種類多達25種, 而在溫帶北大西洋區(qū), 僅有5種海草[3]。我國海草床主要有南海海草分布區(qū)和黃渤海海草分布區(qū), 共有10屬22種, 大約為全球海草種類的30%[4-5]。全球海草床覆蓋面積約為(3～6)×105km2[6-7],據(jù)估算其生態(tài)系統(tǒng)服務價值約為每年每公頃34 000美元[8]。海草生態(tài)系統(tǒng)具有極其復雜的結構, 可以提供多種生態(tài)功能[9], 為海洋生物提供棲息地[10-11]和食物來源[12]。海草床還具有重要的碳儲存功能, 近年來, 海草床“藍碳”功能越來越受到學術界的重視[13-16]。

海草是沿海生態(tài)系統(tǒng)中重要的碳匯[17], 可以通過光合作用吸收CO2[18]。通常情況下, 海草所固定的碳含量大于其代謝需要[19], 多余的有機碳大部分被運輸?shù)胶２莸母案鶢钋o, 最終通過環(huán)境作用將有機碳固存于沉積物中[20]。海草床可以通過釋放生物質或者從凋落物釋放溶解有機碳[21-22], 并通過水流作用輸運到其他生態(tài)系統(tǒng)[23], 全球海草床年輸出的溶解性有機碳高達(1.6～3.3)×108MgC[19], 約占全球海草凈初級生產力的46%[24]。Su等對廣西珍珠灣海草床及其周圍沉積物有機碳儲量進行分析, 發(fā)現(xiàn)海草床沉積物有機碳含量顯著高于無海草區(qū)域[25]。海草碎屑具有大量穩(wěn)定組分和高沉積速率, 沉積物中的厭氧環(huán)境不利于微生物的生長, 使得沉積物有機碳長期儲存[17, 26-28]。全球海草床不到海洋總面積的0.2%, 但全球海草床沉積物有機碳儲量為139.7 MgC/ha, 并且每年碳埋藏量為(2.7～4.4)×107MgC, 占到每年全球海洋碳匯的10%～18%[7, 20, 29], 顯著高于大部分陸地生態(tài)系統(tǒng)[30], 可以緩解全球氣候變化及其帶來的負面影響[31]。我國海草床每年碳匯量約為(3.2～5.7)× 105MgC[32]。山東桑溝灣鰻草海草床生態(tài)系統(tǒng)每年總固碳量約為290 MgC, 吸收碳的形式包括海草固碳、附生植物固碳、海草床捕獲顆粒碳等, 其中, 海草固定的碳占到總固碳量的46%, 為54.35 MgC/ha[33]。通常溫帶地區(qū)海草床有機碳儲量要高于熱帶地區(qū), 可能是因為熱帶地區(qū)海草可以為更多生物提供食物和更高的海草碎屑分解速率[34-35]。我國海南島沿岸現(xiàn)存海草床面積約48.646 7 km2[36], 表層5 cm沉積物有機碳總儲量為40858.5 MgC, CO2吸附量為(1.44± 0.03) MgC/ha, 其中東水、抱才、黃龍、鶯歌等8個海草床沉積物平均碳儲量為7.02 MgC/ha, 總儲量約為1306.45 MgC[37-38]。本文根據(jù)海草床沉積物有機碳的相關研究, 分別從海草床沉積物有機碳來源、組分以及儲量進行綜述, 討論影響海草床沉積物有機碳的主要環(huán)境因素, 結果將為海草床沉積物有機碳相關研究提供科學依據(jù)。

1 海草床沉積物有機碳研究進展

1.1 沉積物有機碳來源

1.1.1 海洋沉積物有機碳來源

沉積物有機碳不僅是水體污染物遷移的重要媒介, 還參與地球化學循環(huán), 對生物地球化學循環(huán)、沉積物演變等有重要的指示作用[39]。沉積物有機碳參數(shù)主要包括碳氮比、碳同位素等, 儲存著氣候、環(huán)境變化的信息等[40-41]。對于海洋中沉積物來源, 科學家一般采用碳氮比(C/N)、碳穩(wěn)定同位素法(δ13C)以及生物標志法(如脂類和木質素)等進行研究。研究發(fā)現(xiàn)陸源和海源有機碳具有一定差別, 陸源C/N比大于12, δ13C為–28‰ ～ –25‰, 海源C/N比值為6～9, δ13C為–19‰ ～ –12‰[42, 43]。Liu等(2020) 采用碳氮穩(wěn)定同位素法和碳氮比法對黃海南部表層沉積物進行研究, 發(fā)現(xiàn)該地區(qū)沉積物有機碳來源組成為海洋、陸地及人為輸入, 且黃河三角洲北部沉積物有機質陸源貢獻較高(>50%), 而在近海泥區(qū)有機質貢獻主要來源于海洋(>70%)[44]。紅樹林生態(tài)系統(tǒng)的碳儲存通常采用穩(wěn)定同位素法和表層沉積物碳氮比方法進行研究[45], 紅樹林對來源于陸地的土壤礦物質有較好的沉降作用, 在河流侵蝕率高的地區(qū), 紅樹林沉積物有機碳有三分之二來源于陸地[46]; 而在侵蝕率低、河流輸入少的環(huán)境下, 紅樹林有機碳有三分之二來源于其本身[45]。Tanaka等(2011)對珊瑚礁溶解有機碳研究, 發(fā)現(xiàn)有機質是從底棲生物群落中釋放的[47]。而珊瑚礁中幾種有機質的來源主要包括珊瑚-蟲黃藻共生群落[48-49]、海草[50]、底棲藻類[51]的釋放以及細菌溶解沉積物有機質釋放[52]?？茖W家還發(fā)現(xiàn)海源和陸源有機質中的溴元素(Br)存在顯著差異[53-54], 相關研究采用溴與有機碳(Br/TOC)的關聯(lián), 分析海源及陸源對沉積物有機碳的貢獻[55-56]。通常湖泊地質、土壤、河床的Br/TOC比值為0.02～2.8 mg Br/g TOC, 而海岸帶沉積物的Br/TOC要顯著高于陸源沉積物, 高達7.6 mg Br/g TOC[57]。

1.1.2 海草床沉積物有機碳來源

海草床沉積物中的有機碳不僅來自于海草, 還來源于陸生植物碎屑和海洋生物, 如浮游植物、大型藻類、附生植物和底棲藻類[58-59]。天然碳同位素的差異是由于植物在進行光合作用的過程中對碳的吸收機制不同所引起的, 由這種機制差異將植物分為C3、C4和CAM植物[60], 因此, 可以通過其本身的同位素特征值(δ13C和δ15N)來測定沉積物有機碳的來源及不同植物的貢獻[61-62]。有關研究發(fā)現(xiàn), 海草的δ13C為–8.99‰, 大型海藻為–13.61‰[63]。Liu等利用碳穩(wěn)定同位素方法對新村灣海草床有機碳來源進行分析, 發(fā)現(xiàn)沉積物有機碳穩(wěn)定同位素值介于–20.39‰ ～ –7.39‰之間, 并且從營養(yǎng)鹽濃度相對較低的海草床到高營養(yǎng)鹽海草床的沉積物中, 大型海藻及附生藻類對沉積物有機碳的貢獻增加了16%, 表明大型海藻及附生藻類對沉積物有機碳的貢獻與營養(yǎng)鹽濃度呈正相關[63]。但是, 同位素法本身存在一定缺陷, 海草與其他藻類可能存在δ13C值重疊的情況[63-64], 導致分析結果偏差。Rahayu等(2019)采用穩(wěn)定同位素標記法及碳氮比分析, 對印度尼西亞群島的海草床研究發(fā)現(xiàn): Barranglompo、Sarappokeke和Kapoposang島的海草床沉積物有機碳具有相似特征, 并且來源于海草的有機碳占到了75%[65]。但在同一研究中, Bauluang島與其他3個島嶼海草床沉積物有機碳主要來源不同, 浮游植物對沉積物有機碳貢獻最大, 約為44%。初級生產者合成的脂肪酸有一些是特定的, 可以用于區(qū)分微藻[66]、大型海藻[67]、被子植物[68]以及原核生物[69], 通過脂肪酸標記法來確定初級生產者到初級消費者的食物鏈結構日益受到關注[70], 采用脂肪酸標記法與穩(wěn)定同位素法聯(lián)用以克服δ13C重疊的問題[71-72], 不同植物的碳、氮穩(wěn)定同位素特征值及特征脂肪酸詳見表1。海草葉片主要由多糖組成, 其余物質主要為木質素、單寧和游離的脂所結合成的酚酸[73-74]。現(xiàn)有研究采用PY-GC-MS和THM-GC-MS兩種熱解技術對大洋波喜蕩草進行有機質解析, 發(fā)現(xiàn)海草不僅由碳水化合物及木質素組成, 還主要由在維管植物中不常見的對羥基苯甲酸(p-HBA)類物質組成。同樣, 該區(qū)域海草床沉積物碎屑中主要由酚類物質p-HBA及碳水化合物組成, 證實海草床沉積物碎屑主要來源于海草的根、莖、葉[75]。

表1 海草、海藻及陸地植物碳、氮穩(wěn)定同位素特征值及特征脂肪酸

1.2 海草床沉積物有機碳分類

沉積物有機碳可以根據(jù)物理、化學、生物(微生物降解性)方法分組。沉積物有機碳分類方法詳見表2。粒度分組法自20世紀60年代開始出現(xiàn), 按照與有機碳結合的顆粒大小, 可分為砂礫(53～2 000 μm)、粗粉粒(5～53 μm)、細粉粒(2～5 μm)、粗黏粒(0.2～2 μm)和黏粒(<0.2 μm)[84]。將有機碳按照密度分, 可分為輕組碳和重組碳[85]。通過化學方法將沉積物有機碳分為活性有機碳(Labile organic carbon, LOC)和惰性有機碳(Recalcitrant organic carbon, ROC), 活性有機碳的生物活性高, 礦化速率高而惰性有機碳則較低[86]?；钚杂袡C碳按照提取方式可以分為鹽提取碳、水提取碳、氯仿提取碳、酸提取碳[87]。根據(jù)其溶解性和水解性又分為溶解有機碳(Dissolved organic carbon, DOC)、酸水解有機碳[86]。生物分組法通常將有機碳分為微生物量碳(Microbial biomass carbon, MBC)和可礦化碳。沉積物中的細菌、真菌、藻類等含有的碳稱為微生物量碳[88], 那些可以被微生物分解且向大氣中釋放CO2的有機碳稱為可礦化碳[89]。多數(shù)研究中根據(jù)其礦化速率將其分為活性有機碳和惰性有機碳[90], 有機碳是否容易降解是區(qū)分活性有機碳和惰性有機碳的依據(jù), 有機碳礦化速率對沉積物有機碳來源變化響應迅速[91]。表示海草床有機碳活性的指標通常用微生物量碳和溶解有機碳[63, 92]。海草地下生物量含有相對較高的碳氮比值、生物可利用性較差, 因此, 海草床固定的碳一般為惰性有機碳[93]。

1.3 海草床沉積物有機碳儲量

學術界將海草和海草床沉積物中的有機碳儲量進行了量化研究(表3)。估算海草床沉積物有機碳埋藏速率主要利用的是14C和210Pb測年技術或通過海草床年際生產力調查等方法[94]。國內外通用的海草床沉積物有機碳儲量計算方法為: 采集一定深度的沉積物樣品, 將其分為相同厚度的子樣、測量容重、沉積物有機碳含量測定、沉積物有機碳密度計算、相同厚度子樣有機碳儲量計算、總樣品有機碳儲量計算。容重的測量是將一定深度的風干沉積物樣本放入到固定體積的容器中, 測定其質量, 計算方法為:

表2 沉積物有機碳分類

表3 全球海草床沉積物有機碳儲量

續(xù)表

使用元素分析儀測定沉積物中有機碳含量, 計算一定深度下沉積物有機碳的密度, 計算方法為:

沉積物有機碳密度=有機碳含量×干容質量.

一定深度沉積物有機碳儲量的計算方法為:

沉積物有機碳儲量=沉積物有機碳密度×沉積物子樣厚度

通過對某一柱狀樣所有沉積物子樣有機碳儲量的總和, 得到采樣地區(qū)該深度下沉積物有機碳的總儲量[95-96]。

1.3.1 不同地區(qū)海草床沉積物有機碳儲量

地中海海草床沉積物有機碳儲量較高, 為372.4 MgC/ha[29]; 佛羅里達灣的海草床沉積物有機碳略高于全球平均值(139.7MgC/ha), 約為175.0 MgC/ha[97]; 而巴西南海岸、海南新村灣與宣德礁有機碳儲量約為67.6 MgC/ha, 顯著低于全球平均值; 東亞、東南亞和澳大利亞海草床的沉積物有機碳儲量約為全球平均水平的25%[98-99]。不同地區(qū)同種海草之間的有機碳儲量也存在顯著差異, R?hr等對溫帶鰻草海草床沉積物有機碳儲量研究發(fā)現(xiàn), 地中海鰻草海草床沉積物有機碳儲量高達357.1 MgC/ha; 太平洋東部和西部鰻草海草床沉積物有機碳儲量分別為69.4 MgC/ha和93.8 MgC/ha; 大西洋東部和西部鰻草海草床沉積物有機碳與太平洋東部相近, 分別為55.4 MgC/ha和54.0 MgC/ha; 而波羅的海鰻草海草床沉積物有機碳儲量最低, 僅為23.1 MgC/ha[100]。

1.3.2 相近區(qū)域不同種類海草床沉積物有機碳儲量

研究發(fā)現(xiàn), 相近區(qū)域不同海草種類的沉積物碳儲量不同。例如, Lavery等(2013)對澳大利亞不同種類海草床進行調查研究發(fā)現(xiàn), 澳洲波喜蕩草的沉積物有機碳含量相對較高, 卵葉喜鹽草、牟氏鰻草、齒葉絲粉草和單脈二藥草的沉積物有機碳含量相對較低, 而泰來草和圓葉絲粉草等顯著低于以上海草[98]。Potouroglou等(2021)對英格蘭海草床沉積物有機碳進行調查, 牟氏鰻草海草床沉積物有機碳含量為68.90±42.10 MgC/ha, 要高于鰻草海草床(23.11±8.17) MgC/ha[101]。而對地中海區(qū)域的研究發(fā)現(xiàn), 大洋波喜蕩草海草床沉積物有機碳含量相比于鰻草海草床相對較高[29, 100]。位于印度尼西亞群島的Kapoposang島和Sarappokeke島海草床沉積物有機碳儲量存在明顯的差異, Sarappokeke島的海草優(yōu)勢種為圓葉絲粉草和單脈二藥草, 沉積物有機碳儲量顯著低于以海菖蒲和泰來草為優(yōu)勢種的Kapoposang島[65, 102]。

2 海草床沉積物有機碳影響因素

2.1 物理因素

2.1.1 沉積物類型

沉積物類型可能會影響沉積物有機碳儲量[116]。美國佛羅里達海草床沉積物有機碳儲量顯著高于巴西東南部海岸, 這主要是因為佛羅里達與巴西東南部海岸沉積物類型分別為碳酸鹽與硅酸鹽[97]。鈣化與沉積作用會加速碳酸鹽沉積物的缺氧, 增強有機碳的保存, 并且當海草凋落物上覆蓋礦物基質時, 有機碳更難被分解[117, 118]。巴西東南部海岸缺乏鈣化和碳酸鈣的儲備, 使得有機碳的代謝與大氣二氧化碳交換、碳酸鹽流動之間存在直接聯(lián)系[97]。

2.1.2 空間分布

海草床的水平屬性(相對邊緣的距離)是海草生態(tài)系統(tǒng)碳儲量空間異質性的重要決定因素, 研究發(fā)現(xiàn), 海草床邊緣區(qū)域沉積物有機碳儲量高于裸露沉積物約3倍, 而海草床內部沉積物有機碳儲量更要顯著高于邊緣[119]。大型海草沉積物有機碳儲量要大于小型海草或無海草區(qū)域[120], 這主要是因為結構較大、埋藏較深的根莖組織可以對沉積物起到保護作用以保存有機碳和截獲更多懸浮顆粒[121-123], 有效光照輻射是影響海草碳儲存能力的關鍵因子, Collier等研究發(fā)現(xiàn)生長在2 m水深的波狀波喜蕩草地上部分生物量(899 gDW/m2)、地下部分生物量(1 028 gDW/m2)以及海草密度(1 435 shoots/m2)均顯著高于8 m水深處海草(47 gDW/m2; 43 gDW/m2; 80 shoots/m2)[123]。海草床沉積物有機碳儲量與所在區(qū)域的深度呈現(xiàn)顯著相關性, 生長在2～4 m水深的波狀波喜蕩草海草床沉積物有機碳儲量為生長于6～8 m水深區(qū)域的4倍, 而位于水深 2 m和32 m處的大洋波喜蕩草海草床沉積物有機碳儲量相差10倍以上[116]。

2.1.3 溫度升高

全球氣溫升高會對海草床有機碳儲量產生一定影響。全球溫度升高將顯著提高沉積物有機碳的礦化速率[124-125]。研究發(fā)現(xiàn)溫度每上升10 ℃, 碳的礦化速率可提升4.5倍[124]。自養(yǎng)生物的呼吸速率要小于其吸收二氧化碳的速率, 異養(yǎng)生物則相反[126], 溫度升高的情況下, 呼吸速率的增加量要顯著高于二氧化碳的吸收速率[127-128], 氣候變暖可能使得自養(yǎng)生態(tài)系統(tǒng)向異養(yǎng)生態(tài)系統(tǒng)轉變, 從而發(fā)生碳匯到碳源的轉變[127]。海草生態(tài)系統(tǒng)的甲烷年排放量達0.09～2.7 Tg, 海草床沉積物甲烷的釋放速率隨著海水溫度的升高而增加[129]。紅海的海草生態(tài)系統(tǒng)已經(jīng)在溫度較高的夏季從自養(yǎng)狀態(tài)向異養(yǎng)狀態(tài)改變[130]。Burkholz等研究發(fā)現(xiàn), 在溫度從25℃上升到37 ℃的過程中, 有海草覆蓋區(qū)域的沉積物甲烷和二氧化碳釋放速率為無海草覆蓋區(qū)域的10～100倍, 并且溫度升高導致甲烷和二氧化碳通量顯著增加[131]。另外, 海洋沉積物微生物活性隨著溫度升高而增強, 導致在較高的溫度下沉積物有機碳水解和發(fā)酵速率都超過了正常條件[132]。

2.1.4 自然與人為擾動

臺風伴隨的強降雨會對沉積物表面造成明顯的擾動[133-134], 降雨對沉積物造成的擾動為正常情況下的100倍[135], 并且暴雨會導致沉積物中有機碳的氧化方式發(fā)生改變, 從而造成沉積物有機碳加速分解。Sampere等對大陸邊緣表層沉積物中有機質的木質素研究, 發(fā)現(xiàn)颶風過后來自海灣和沿海濕地的有機碳輸入可能會迅速分解[136]。海平面上升會導致沿海地區(qū)沉積物有機碳大量釋放到臨近河口及開闊水域[137-138], 這可能會改變河口及開闊水域微生物群落及活性, 進一步造成沉積物有機碳降解。Aoki等對美國弗吉尼亞州的鰻草海草床沉積物調查發(fā)現(xiàn), 海洋熱浪發(fā)生3年后沉積物有機碳含量下降近20%, 海草密度下降90%, 并且海草床衰退后沉積物有機碳的恢復呈現(xiàn)滯后性[114]。

人為的干擾也會造成海草床沉積物有機碳損失。例如, 疏浚工程、挖沙以及船只活動會引起海水沉積物擾動, 導致海水渾濁度升高, 從而危害海草生長[139-141]。海草床衰退導致海草床碳儲存功能減弱, 使得原本存儲于海草床中碳再次釋放, 釋放量高達(1.5～9.0) ×107MgC[142]。船只擱淺所造成的有機碳損失量最高, 約為57.1 MgC/ha[143]。海草床內頻繁的灘涂漁業(yè)活動會擾動沉積物, 造成海草床沉積物有機碳儲量降低[144]。海草床沉積物有機碳含量與沉積物深度呈顯著負相關, Macreadie等發(fā)現(xiàn)活性有機碳含量與沉積物深度呈顯著負相關, 活性有機碳含量從表層的43%下降至深層(80 cm)的3%, 深層的有機碳暴露于空氣中會顯著增加微生物豐度, 加速有機碳礦化和周轉, 表明沉積物的擾動會引起海草床有機碳減少[145]。Thorhaug等對墨西哥近岸海草床進行調查, 發(fā)現(xiàn)人為干擾后海草床沉積物有機碳損失量平均值為(20.98±7.14) MgC/ha, 并且在海草床修復工程中所恢復的有機碳平均值高達(20.96±8.59) MgC/ha[143]。得克薩斯州Predator地區(qū)的海草床修復過程海草存活率高達90.7%, 顯著增加了當?shù)睾２莞采w度[146], 但該地區(qū)海草修復工程對有機碳的恢復效果并不顯著, 其每年對沉積物有機碳的固定量僅為0.5 MgC/ha[143]。學術界需要對海草床修復工程運行過程及后期可能對海草床碳通量產生的影響進行評估, 為政府平衡投入與收益間的關系提供依據(jù)。

2.2 化學因素

2.2.1 海洋酸化

海洋酸化可以引起海草生物量和密度增加, 從而加強其對有機碳的埋藏能力[147]。在溫帶以及熱帶的高二氧化碳區(qū)域, 都出現(xiàn)了海草密度以及生物量上升的情況[148]。但是, Apostolaki等研究發(fā)現(xiàn), 與較低的二氧化碳區(qū)域相比, 地中海中高二氧化碳區(qū)域海神草生物量反而減少[149]。Vizzini等通過結合海草床植物以及沉積物性質對希臘Milos島和意大利Vulcano島的2個高二氧化碳區(qū)域進行調查, 發(fā)現(xiàn)Vulcano島的海草生物量以及葉片面積減小, 可能會對沉積物表層有機碳的積累造成負面影響; 而在Milos島, 雖然海草的生物量、葉面積均上升, 但是表層沉積物有機碳含量下降[150]。在較低pH值情況下, 細菌胞外酶活性增加, 加速高分子有機物向低分子有機物分解的過程, 可能降低海草床的碳儲存能力[151, 152]。

2.2.2 富營養(yǎng)化

沿海水域的養(yǎng)分富集會降低海草床的碳匯能力[153]。營養(yǎng)鹽濃度過高會導致海草氨中毒, 或者引起大型海藻爆發(fā)限制海草的光合作用[154-155], 降低海草生物量[156], 使得海草對沉積物有機碳的貢獻減少[157]。營養(yǎng)鹽濃度增高會影響浮游細菌的活動, 改變細菌群落, 加速溶解性有機碳的分解[158-159]。Liu等發(fā)現(xiàn), 當海草床處于高營養(yǎng)鹽濃度環(huán)境下, 具有降解難降解化合物能力的微生物如酸微菌(Acidi-mi--cro-biia)、疣微菌(Verrucomicrobiales)以及微球菌(Micro-coc-ca-les)的豐度增加, 從而減弱海草床長期固存有機碳的能力[44]。

2.3 生物因素

2.3.1 微生物因素

沉積物中有機碳長期儲存的因素主要是因為厭氧環(huán)境不利于微生物生長以及海草碎屑不易分解[17, 26-28]。然而, 全球海草床每年的有機碳損失高達2.99×108MgC[29]。大量研究表明, 富營養(yǎng)化、全球變暖、植物入侵、人為干擾都會影響海草床中微生物群落特征[160-161], 微生物控制著關鍵的生物地球化學途徑, 因此, 微生物活性和群落結構的變化會影響藍碳的穩(wěn)定性, 微生物的呼吸以及活性的增強會導致有機碳礦化速率提高, 從而加速碳的流失[162-164]。

2.3.2 底棲生物

小型底棲動物對沉積物的擾動會增加沉積物的孔隙度與含氧率, 并且小型底棲動物如線蟲會釋放粘液, 為細菌的生長發(fā)育創(chuàng)造條件[165], 顯著提高微生物的豐度與活性[166-167]。大型底棲動物會通過抑制或激活微生物基團來影響沉積物中微生物群落[168]。Lacoste等發(fā)現(xiàn), 大型底棲動物對沉積物的擾動會造成細菌活性的增強, 這可能會加速有機碳的降解[169]。

2.3.3 藻類爆發(fā)

由富營養(yǎng)化和全球氣候變化協(xié)同影響下引起的附生藻類的大量繁殖會在一定程度上保護海草, 并且增加海草床沉降懸浮顆粒物的能力[170-171], 但是附生藻類和大型海藻暴發(fā), 會通過與海草競爭營養(yǎng)鹽、形成缺氧環(huán)境、影響光照等途徑造成海草衰退[157]。由于海草床的加速減少, 近岸海域更容易受到氣流和波浪的影響, 這會導致海草床中儲存的有機碳大量減少[172]。當營養(yǎng)鹽濃度升高時, 大型海藻和附生藻類對沉積物有機碳的貢獻短時間內會相對增加[27], 向水體中大量釋放碳水化合物與氨基酸[173-174], 導致微生物所能利用有機碳的源發(fā)生改變[153], 引起海草床長期存儲有機碳的能力降低。與海草相比, 來源于附生藻類和大型海藻的有機碳更容易分解[175], 會在幾天內被細菌迅速利用[176], 大量多糖及纖維素的加入, 會引起沉積物中蔗糖酶與纖維素酶活性的顯著上升[177], 增加原有有機碳的分解, 導致海草床碳儲量減少[178-179]。

3 展望

綜上所述, 國內外學術界對海草床沉積物有機碳來源、儲量以及影響因素等方面已經(jīng)展開了很多研究, 但是相關研究仍有待加強。未來海草床沉積物有機碳研究應該在以下幾個方面展開:

(1) 加強海草床碳通量普查和海草床調查。調查全國各海草床海草地上地下部分生物量和沉積物中有機碳的來源、組份及儲量, 明確全國海草床沉積物碳儲存的基本情況。

(2) 分析全球氣候變化背景下沉積物有機碳的變化機制。在全球氣候變化背景下, 研究海草床有機碳來源、組分, 沉積物中微生物、酶活性變化等, 明確海草床中有機碳的變化機制, 為海草床沉積物有機碳的科學管理提供科學對策。

(3) 研究影響海草床碳儲量的主要環(huán)境因素。對處于富營養(yǎng)化以及其它人類活動影響下的海草床沉積物進行碳儲量的長期觀測, 利用野外操控實驗和室內模擬實驗, 明確環(huán)境因素對沉積物有機碳儲量的影響機制。

(4) 明確海草床修復工程對沉積物有機碳儲存的長期響應, 尤其是對海草床修復工程運行過程及后期對海草床碳通量的可能影響進行評估, 分析海草床修復工程在碳匯方面的實際收益, 為平衡海草床修復工程的投入與收益提供科學依據(jù)。

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Review of organic carbon in seagrass bed sediment

YE Jia-hui, QIU Chong-yu, ZENG Wen-xuan, SHI Yun-feng, ZHAO Mu-qiu, HAN Qiu-ying

(Yazhou Bay Innovation Institute, Key Laboratory of Utilization and Conservation for Tropical Marine Biore-sources of Ministry of Education, Key Laboratory for Coastal Marine Eco-environment Process and Carbon Sink of Hainan Province, Hainan Tropical Ocean University, Sanya 572022, China)

Seagrass beds provide important ecosystem services, such as supporting biodiversity and providing carbon storage. Several scientists have studied the carbon storage mechanisms of seagrass beds. The annual carbon sequestration of seagrass beds is (2.7～4.4)×107MgC. Recently, seagrass beds have declined worldwide due to human activities, resulting in organic carbon storage reduction in seagrass sediment. This paper reviewed the research advancements of sediment organic carbon in seagrass beds, including the sources, components, storage, and environmental indicators. The environmental variations affecting carbon storage in seagrass beds were discussed from the three aspects of physics, chemistry, and biology. Finally, the primary research directions for the future study were proposed, including strengthening the carbon flux survey of seagrass beds, exploring the mechanism of sediment organic carbon change due to global climate change, defining the rate of carbon storage loss in seagrass beds, and studying the impact of coastal zone engineering on sediment organic carbon. Evaluating carbon storage mechanisms will provide the scientific basis for the blue carbon study in the oceans globally.

seagrass beds; sediment organic carbon; source; storage; environmental effects

Aug. 15, 2021

P76

A

1000-3096(2022)09-0130-16

10.11759/hykx20210815001

2021-08-15;

2022-01-18

海南省高層次人才項目(420RC657); 國家自然科學基金(41730529, 41766004); 海南熱帶海洋學院科研啟動項目(RHDXB201710)

[the High-level Talents Project of Hainan Province, No. 420RC657; the National Natural Science Foundation of China, Nos. 41730529, 41766004; the Project of Hainan Tropical Ocean University, No. RHDXB201710]

葉嘉暉(1997—), 男, 浙江余姚人, 碩士研究生, 主要從事海洋生態(tài)學研究, 電話: 15958810658, E-mail: 850273277@qq.com; 韓秋影(1980—),通信作者, 女, 吉林德惠人, 博士, 研究員, 研究方向: 海洋生態(tài)學, 電話: 13006036262, E-mail: hanqiuying0312@sina.com

(本文編輯: 康亦兼)