水處理外文翻譯---不同水處理工藝對藍藻毒素的去除效果研究

1、<p><b>　　2．英語論文翻譯</b></p><p>　　Elimination of microcystins by water treatment processes— examples from Sulejow Reservoir, Poland</p><p>　　4. Discussion</p><p>　　The

2、 conventional water treatment process using preoxidation,coagulation, sand filtration, ozonation and chlorination in the Sulejow-Lodz waterworks system,and coagulation, sedimentation, sand filtration, ozonation and chlor

3、ination in the Tomaszow-Lodz waterworks system were effective in the elimination of extracellular and cell-bound microcystins. These twowaterworks had similar, rather simple treatment processes. The health hazard caused

4、by microcystins in the water used for drinking water prod</p><p>　　Cyanobacterial toxins can enter a water treatment plant in two forms, either as intracellular toxins (bound within the cyanobacterial cells)

5、 or as extracellular (dissolved) toxins. An elevated level of extracellular toxins was observed in Sulejow Reservoir in 2002 (Table 3a—e.g. 13 August 2002). The high concentration of free toxin in raw water could be expl

6、ained by a collapsing cyanobacterial bloom and a lysis of cyanobacterial cells. Although the studied water utilities could eliminate extrace</p><p>　　In this study, the most effective step of the treatment p

7、rocess in the removal of microcystins was the filtrationprocess, which reduced microcystins by 75.4% compared to the concentration at the end of the preceding step (Fig. 4). Rapid filtration, a method usually employed af

8、ter coagulation to remove the flocculants, does not effectively remove cyanobacterial cells (Lepisto et al., 1994; Steffensen and Nicholson, 1994). The efficiency of sand filtration, reported by Hoeger et al. (2004) in t

9、he </p><p>　　The concentration of microcystins can be effectively reduced also by activated carbon filtration. From water treatment studies conducted at the laboratory and pilotplant scale it was concluded t

10、hat granular activated carbon (GAC) filtration is effective in removing cyanobacterial toxins from drinking water (Hoffman, 1976; Falconer et al., 1983; Keijola et al., 1988; Falconer et al., 1989; Himberg et al., 1989;

11、Mereish and Solow, 1989; Donati et al., 1994; Lambert et al., 1996). Powdered activate</p><p>　　The use of chlorine dioxide in this study for a preoxidation process (1.6–2.8 mg l_1 for a contact time of 30 m

12、in) caused a reduction of total microcystin concentration by 40.4% (78.2% reduction for cell-bound microcystins and 17.2% increase for dissolved forms) (Fig. 4). These findings are in accordance with results presented by

13、 Nicholson et al. (1994). Tsuji et al. (1997) showed that a chlorine dose of 2.8 mg l_1 for a contact time of 30 min was sufficient for a 99% destruction of MC-LR. Pre-o</p><p>　　Coagulation and flocculation

14、 are defined as a process in which suspended particles are aggregated through the addition of a chemical coagulant. Coagulants used for this purpose (especially aluminium sulphate dosed at 100–160mg l_1 in 2002 and also

15、polyaluminium chloride</p><p>　　used in 2003 dosed at 120–150 mg l_1) caused a reduction of microcystins, mainly cell-bound microcystins, by 37.9% in 2002 compared to the preceding step. This process is inef

16、fective in the removal of extracellular cyanotoxins (Keijola et al., 1988; Himberg et al., 1989; Lambert et al., 1996; Chow et al., 1998). However, it can be effective in removing intracellular cyanotoxins through the re

17、moval of intact cyanobacterial cells. Coagulation is considered an efficient method for elimination of cy</p><p>　　may cause additional problems such as lysis ofcyanobacterial cells leading to a release of t

18、oxins (James and Fawell, 1991).</p><p>　　In the studies presented here chlorine and ozone were only used as disinfectants and for colour and/or odour removal in the last steps of the water treatment processe

19、s. The efficiency of chlorination seems to depend largely on the chlorine compounds and the concentration used. Aqueous chlorine and calcium hypochlorite with contact time of over 30 min at a concentration of 1mg l_1 rem

20、oved more than 95% of microcystins (Himberg et al., 1989; Nicholson et al., 1993; Nicholson et al., 1994; Rositano</p><p>　　Ozonation can be effective for the destruction of microcystins since it is one of t

21、he most powerful oxidants. Several studies have shown that the toxin removal is strongly dependent on the concentration of ozone (Hart and Scott, 1993; Fawell et al., 1993; Carlile, 1994; Rositano, 1996; Croll and Hart,

22、1996; Hart et al., 1997; Rositano et al., 2001). Keijola et al. (1988) showed that ozonation process at dose of 1mg l_1 was sufficient to completely remove microcystins. Further studies by Himberg </p><p>　　

23、The management strategy of the water utilities includes mixing of surface water and ground water from 7 deep wells located near Sulejow Reservoir (Table 3). The use of ground water reduces problems caused by the presence

24、 of toxic cyanobacterial blooms in surface water. The increased use of groundwater by the Sulejow-Lodz waterworks reduced microcystins in water on entry and during treatment process. The Sulejow-Lodz water treatment plan

25、t was effective in the elimination of intracellular as well </p><p><b>　　漢語翻譯：</b></p><p>　　不同水處理工藝對藍藻毒素的去除效果研究</p><p>　　—以波蘭蘇爾水庫為例</p><p><b>　　4 討論&l

26、t;/b></p><p>　　Sulejow-Lodz水處理廠采用傳統(tǒng)的水處理方法經(jīng)過預(yù)氧化 混凝 沙慮 氧化 氯消毒，Tomaszow-Lodz水處理系統(tǒng)采用混凝 沉淀 氧化 消毒也可以有效去除胞內(nèi)與胞外的藍藻毒素，這兩做水廠采用相似的水處理流程，由藍藻毒素一起的健康問題在Sulejow-Lodz水處理系統(tǒng)中更為嚴重，因為該水廠的取水口位于蘇爾水庫狹窄的港灣處，浮游生物在此大量出現(xiàn)。</p>

27、<p>　　Tomaszow-Lodz水廠的取水口位于Pilica河，由浮游生物引起的問題較少，在這兩個水處理系統(tǒng)中對藍藻毒素有較好的去除效果，在澳大利亞水處理廠也有相同的報道</p><p>　　浮游生物有毒物質(zhì)以胞內(nèi)或溶解與水體中兩種形式進入水處理構(gòu)筑物，2002在蘇爾水庫中觀測到了較高水平的胞外有毒物質(zhì)，極有可能是由于細胞的破碎與溶解所導(dǎo)致。既是由于本研究的水處理構(gòu)筑物可以有效的去除胞外藍藻毒

28、素，但高濃度的胞外有毒物對簡單的水處理構(gòu)筑物來說仍然是一個較難的問題。</p><p>　　在本次研究中對藍藻毒素去除效率最高的處理過程為過濾，它使藍藻毒素的濃度下降了75.4%，在混凝之后普遍使用的快速過濾難以有效地去除浮游生物細胞，據(jù)hoger 等人研究混凝結(jié)合沙慮對浮游生物細胞的去除效率可達99.9%。</p><p>　　活性炭吸附可以有效的去除藍藻毒素，試驗研究顯示顆?；钚蕴窟^濾

29、可以有效的去除飲用水中浮游生物產(chǎn)生的有毒物質(zhì)（(Hoffman,1976; Falconer et al., 1983; Keijola et al., 1988; Falconeret al., 1989; Himberg et al., 1989; Mereish and Solow,1989; Donati et al., 1994; Lambert et al., 1996).而粉末活性炭在用于有毒物質(zhì)去除是較常規(guī)工藝時用量較多

30、(Wheeler et al., 1942; Hoffman, 1976;Falconer et al., 1983; Keijola et al., 1988; Himberg et al.,1989)。</p><p>　　二氧化氯用于預(yù)氧化是對對藍藻毒素可達40.4%的去除率，與Nicholson等人的研究結(jié)果相符，當氯的劑量達到2.8mg/l，接觸30min后對MC-LR的去除率達99%，，在混凝之前進行

31、臭氧 氯 高錳酸鉀預(yù)氧化已經(jīng)廣泛被應(yīng)用，尤其是在藻類與浮游生物的去除中，尤以氯 高錳酸鉀預(yù)氧化對藻類細胞的去除率最高，但應(yīng)該盡量避免因預(yù)氧化導(dǎo)致細胞中的有毒物質(zhì)釋放進入水體(Bonne´ lyeet al., 1995; Hrudey et al., 1999; Pietsch et al., 2002)，本次研究中也發(fā)現(xiàn)了同樣的現(xiàn)象，因此對有毒物質(zhì)去除優(yōu)先的水處理應(yīng)避免使用預(yù)氧化，只有在總有毒物質(zhì)濃度較低方可采用。</

32、p><p>　　混凝與絮凝是通過投加化學(xué)物質(zhì)使水中的懸浮物質(zhì)聚合，高過程可以去除部分的藍藻毒素，尤其是胞內(nèi)藍藻毒素的去除率可達37.9%，同時對胞外微囊藻毒素也有一定的去除率(Keijola et al., 1988; Himberg et al., 1989;Lambert et al., 1996; Chow et al., 1998)。他也可以通過去除與其接觸的細胞來去除胞內(nèi)微囊藻毒素。混凝是一種有效去除水體中

33、藍藻的方法，但對可溶性的藻毒素的去除效率較低(James and Fawell, 1991; Rositano and Nicholson, 1994)，對藍藻的去除效果與混凝劑劑量與混凝PH的選擇相關(guān)，然而混凝可能導(dǎo)致細胞破碎而使胞內(nèi)有毒物質(zhì)進入水中(Jamesand Fawell, 1991)。</p><p>　　因此臭氧氧化與氯氧化僅用于水處理后期色度或臭味的去除，氯氧化的效果與氯的藻類和使用量相關(guān)，液氯

34、與次氯酸鈣當接觸時間超過30分鐘，濃度達1mg/l 時可達95%的藍藻毒素去除率(Himberg et al., 1989; Nicholson et al.,1993; Nicholson et al., 1994; Rositano and Nicholson,1994; Carlile, 1994)。</p><p>　　由于臭氧是一種很強的氧化劑，因而臭氧氧化可以有效的除去微囊藻毒素，研究顯示去除效果與濃

35、度息息相關(guān)(Hart and Scott, 1993; Fawell et al., 1993;Carlile, 1994; Rositano, 1996; Croll and Hart, 1996;Hart et al., 1997; Rositano et al., 2001). Keijola et al.(1988)，當濃度達到1mg/l 是即有良好的處理效果，Himberg的深入研究也證明了該觀點。</p>&l

36、t;p>　　水廠的管理方法為地表水與蘇爾水庫附近七口地下水井水的混合，地下水的使用減輕了由藍藻爆發(fā)引發(fā)的藍藻毒素問題。Sulejow-Lodz水廠地下水使用的增加減少進水與各個處理單元的藍藻毒素濃度，在2002-2003中Sulejow-Lodz水處理系統(tǒng)可有效的去除胞內(nèi)與胞外藍藻毒素。蘇爾水庫成為Lodz的可選擇性水源，但仍然是水庫下游Tomaszow-Lodz水處理系統(tǒng)的首選水源，同時該水庫對娛樂業(yè)也非常的重要，因此限制進入該