WO2016019677A1 - 一种菹草发酵液在人工湿地脱氮中的应用 - Google Patents

一种菹草发酵液在人工湿地脱氮中的应用 Download PDF

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WO2016019677A1
WO2016019677A1 PCT/CN2014/094197 CN2014094197W WO2016019677A1 WO 2016019677 A1 WO2016019677 A1 WO 2016019677A1 CN 2014094197 W CN2014094197 W CN 2014094197W WO 2016019677 A1 WO2016019677 A1 WO 2016019677A1
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fermentation
denitrification
water
fermentation broth
valerian
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French (fr)
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杨柳燕
陈乾坤
焦一滢
张权
李丽
陈旭
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Nanjing University
Nanjing Tech University
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Nanjing University
Nanjing Tech University
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    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F3/00—Biological treatment of water, waste water, or sewage
    • C02F3/32—Biological treatment of water, waste water, or sewage characterised by the animals or plants used, e.g. algae
    • C02F3/327—Biological treatment of water, waste water, or sewage characterised by the animals or plants used, e.g. algae characterised by animals and plants
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F3/00—Biological treatment of water, waste water, or sewage
    • C02F3/02—Aerobic processes
    • C02F3/06—Aerobic processes using submerged filters
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F2101/00—Nature of the contaminant
    • C02F2101/10—Inorganic compounds
    • C02F2101/105—Phosphorus compounds
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F2101/00—Nature of the contaminant
    • C02F2101/10—Inorganic compounds
    • C02F2101/16—Nitrogen compounds, e.g. ammonia
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F2103/00—Nature of the water, waste water, sewage or sludge to be treated
    • C02F2103/007—Contaminated open waterways, rivers, lakes or ponds
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F2305/00—Use of specific compounds during water treatment
    • C02F2305/06—Nutrients for stimulating the growth of microorganisms
    • Y—GENERAL TAGGING OF NEW TECHNOLOGICAL DEVELOPMENTS; GENERAL TAGGING OF CROSS-SECTIONAL TECHNOLOGIES SPANNING OVER SEVERAL SECTIONS OF THE IPC; TECHNICAL SUBJECTS COVERED BY FORMER USPC CROSS-REFERENCE ART COLLECTIONS [XRACs] AND DIGESTS
    • Y02—TECHNOLOGIES OR APPLICATIONS FOR MITIGATION OR ADAPTATION AGAINST CLIMATE CHANGE
    • Y02W—CLIMATE CHANGE MITIGATION TECHNOLOGIES RELATED TO WASTEWATER TREATMENT OR WASTE MANAGEMENT
    • Y02W10/00—Technologies for wastewater treatment
    • Y02W10/10—Biological treatment of water, waste water, or sewage

Definitions

  • the invention belongs to the field of environmental engineering, and particularly relates to the application of a sorghum fermentation broth in denitrification of constructed wetlands.
  • the primary A emission standard (TN 15mg/L, NH 3 -N 5(8)mg/L, TP 0.5mg/L) is still much higher than the surface water environmental quality standard (surface water V water standard TN 2mg/L) NH 3 -N 2 mg/L, TP 0.4 (lake 0.2) mg/L).
  • the advanced treatment technologies for tail water in sewage treatment plants mainly include physicochemical methods (filtration, adsorption, etc.), biological methods (bioreactors, biofilters, constructed wetlands, etc.) and membrane separation methods (reverse osmosis, microfiltration, Nanofiltration, etc., in which the constructed wetland technology is widely used due to its low investment and maintenance costs, good nitrogen and phosphorus removal effect, low secondary pollution and landscape effects.
  • VFAs volatile fatty acids
  • VFAs volatile fatty acids
  • the deep denitrification treatment of the tail water can solve the disposal problem of the constructed wetland plants after harvesting, realize the resource utilization of aquatic plants, and have important research significance and application value.
  • Denitrification is the process by which microorganisms convert nitrate nitrogen and nitrite nitrogen into nitrogen and release it into the atmosphere under conditions of no oxygen or low oxygen.
  • the main influencing factors of denitrification and denitrification are dissolved oxygen (DO), pH, temperature, and carbon source.
  • Dissolved Oxygen It is generally considered that denitrification can be carried out normally when dissolved oxygen is kept below 0.5 mg/L. This is because O 2 has higher ability to accept electrons than NO 2 - -N and NO 3 - -N, and when molecular oxygen and nitrate are present simultaneously, denitrifying bacteria preferentially perform aerobic respiration.
  • the optimum temperature for temperature denitrification is 15 to 30 °C.
  • denitrifying bacteria are more sensitive than nitrifying bacteria.
  • seasonal cooling occurs, the denitrification process will be inhibited prior to the nitrification process, and an additional carbon source is needed to improve the denitrification effect.
  • temperature also has a significant effect on microbial activity, which in turn affects the effects of counter-effects.
  • Carbon source is an electron donor in the denitrification process and is also the main source of energy for microbial growth and reproduction. Insufficient carbon source will directly affect denitrification. Adding an external carbon source is one of the effective methods to improve the efficiency of denitrification and denitrification. The type and amount of additional carbon source will have a significant impact on denitrification efficiency.
  • the existing additional carbon sources can be roughly divided into two categories, namely traditional carbon sources and new carbon sources.
  • Traditional carbon sources are mainly liquid organic substances, including low molecular organic substances (such as methanol, ethanol and acetic acid) and sugar substances (such as glucose, sucrose, etc.).
  • the new carbon sources mainly include natural solid organic matter (such as plant straw) rich in cellulosic materials, some degradable artificial materials (such as waste paper, degradable lunch boxes, etc.) and high-carbon industrial wastewater.
  • the sugar substance As an external carbon source, the sugar substance has a better treatment effect and a lower cost. Zhao Li rotating et al. (2006) treated urban polluted river water with constructed wetlands. For sewage with high concentration of nitrogen and nitrogen, the effect of nitrogen removal can be effectively improved by adding glucose. When the wetland C/N is increased from 2 to 8, the TN removal rate is provided from 55%. 89%.
  • CMC Cellulose
  • the optimal glucose dosage for the IVCW system with a treatment capacity of 60 L/d is 1.5 g
  • the mass ratio of glucose to nitrate nitrogen is only 4.3
  • the dosage is much lower than the C/N required for denitrification.
  • glucose is used as a carbon source
  • the microbial cell yield is high, which tends to cause clogging in processes such as artificial wetlands.
  • Cellulose carbon sources are widely available and low in cost.
  • the solid organic carbon sources rich in cellulosic materials currently studied include waste paper, corn stover, wheat straw, straw, and aquatic plant branches or stems such as cattails and reeds.
  • Wen Hui et al. (2011) studied the effect of wheat straw as an external carbon source on the denitrification effect of simulated constructed wetland. The results showed that the optimum condition for removing nitrate nitrogen was 25 °C when the influent nitrate concentration was 30 mg/L.
  • the reaction time is 10 hours, and the mass ratio of wheat straw to water is 1:50.
  • the TN removal rate of the vertical flow constructed wetland is increased from 60% to 80%.
  • the use of cellulose as a carbon source not only has a better denitrification effect, but also is cheap and easy to obtain, and achieves the purpose of waste utilization, which is in line with the development requirements of energy saving and emission reduction and circular economy in China.
  • its drawback is that the release of the carbon source cannot be effectively controlled, the required hydraulic retention time is long, and the effluent water quality is susceptible to external temperature.
  • Valerian has strong vitality and wide adaptability, so it is widely planted in constructed wetlands.
  • Valerian is rich in cellulosic materials. After harvesting, it can produce a large amount of volatile fatty acids (VFAs) and other nutrients through anaerobic fermentation.
  • VFAs volatile fatty acids
  • It is an excellent potential external carbon source and can be used as a carbon source for denitrification to realize the tail of wastewater treatment plant.
  • the deep denitrification treatment of the submerged artificial wetland of water can solve the disposal problem of the constructed wetland plants after harvesting, and realize the resource utilization of aquatic plants.
  • the technical problem to be solved by the present invention is to provide a sorghum fermentation broth as a carbon source, added to a constructed wetland, and used for denitrification treatment of sewage.
  • the yarrow fermentation broth is prepared as follows:
  • the valerian, the activated sludge, and the water are administered in a ratio of 100 kg:1 L:1 L.
  • the acclimation method of the activated sludge is cultured and acclimated by a method known in the art, and the denitrifying microorganism is finally made into a dominant flora by controlling the composition of the acclimated medium and the acclimation temperature, pH, and time; Domestication:
  • composition of the acclimation medium was as follows: glucose 15 g/L, NaNO 3 3.04 g/L, KH 2 PO 4 0.44 g/L, MgSO 4 ⁇ 7H 2 O 0.96 g/L, CaCl 2 0.72 g/L, NaHCO 3 0.96 g /L, MnCl 2 0.11 g / L.
  • the excess sludge dehydrated in a 2.5 kg sewage treatment plant was placed in a 5 L fermentor, 4 L domestication medium was added, the pH was adjusted to 7.4, and the temperature was adjusted at 28 ° C for one week, and the pH was monitored every day.
  • the fermentation temperature is 12 to 30 ° C, preferably 20 to 30 ° C, and most preferably 30 ° C.
  • the fermentation time is 5-10 days, preferably 7 days.
  • the pH during the fermentation is controlled to be 7 to 8, preferably 7 to 7.5.
  • the sewage is the tail water of the sewage treatment plant, wherein the nitrogen content is 10-15 mg/L, preferably 12 mg/L.
  • the sorghum fermentation broth is added to the sewage according to the following addition amount: the ratio of the COD value of the yarrow broth is 8-16, preferably 9-10; and the hydraulic retention time of the tail water is 4-8h, preferably 6h.
  • the raw materials of valerian are widely available and the cost is low.
  • the method for preparing yarrow fermentation broth is simple and easy.
  • Figure 1 is a diagram of a horizontal submerged artificial wetland device
  • Figure 4 NH 3 -N removal rate of subsurface flow constructed wetland
  • the experimental apparatus used in the examples has a structure as shown in FIG.
  • the cloth water area is 5cm long and 15cm wide. It is separated from the treatment area by a perforated plate.
  • the perforated plate is evenly distributed with four circular water holes with a diameter of 2cm from bottom to top.
  • the gravel with a particle size of 3cm is laid in the area. Preliminary filtration to prevent blockage inside the wetlands.
  • the treatment area is 30cm long and 15cm wide.
  • the Tianzhu River in the Xianlin Campus of the University has a plant height of about 50-60 cm and is growing vigorously.
  • the catchment area is 5 cm long and 15 cm wide, separated from the treatment zone by a perforated plate, and a gravel having a particle size of 3 cm is laid in the zone.
  • the instruments used in the examples are: Baoding Lange BT-2 constant current pump, XX magnetic stirrer, 1.5L pumping Filter bottle, 1.25L wow haha pure water bottle, plant crusher, water-proof constant temperature incubator, UV-visible spectrophotometer UV2450, D-1 automatic steam sterilization pot, electronic balance, 25mL with glass grinding mouth colorimetric Tube, quartz cuvette, ultrapure water system (Milli-Q, Millipore), 0.45 ⁇ m water filter.
  • the detection methods of the components of the effluent and the influent of the examples are as follows: (1) TN measurement using potassium persulfate oxidation-ultraviolet spectrophotometry: (2) NO 3 - -N determination by ultraviolet spectrophotometry; (3) NO 2 - Determination -N N- (1- naphthyl) - ethylenediamine spectrophotometry; (4) NH 3 -N was determined by Nessler's reagent Colorimetric: (5) TP was determined by digestion persulfate - ammonium molybdate coloration Method: COD Cr was determined by potassium dichromate method: (6) DO was measured by Hach HQ30d portable dissolved oxygen meter; (7) pH was measured by hash HQ30d portable pH meter.
  • the constructed wetland system needs to be commissioned before the formal test.
  • the system was started in mid-August 2013.
  • a certain amount of activated sludge acclimated with denitrification medium was added to the first three influent waters for microbial inoculation.
  • NaNO 3 was used as the nitrogen source and glucose was used as the carbon source.
  • the concentration of water and nitrogen was 15 mg/L, and the C/N ratio was 8.
  • the effluent water quality was stable, and 4 sets of wetland devices all reached stable operation, and there was no significant difference in nitrogen removal efficiency under the same conditions.
  • the influent water is pumped into the water distribution area of the constructed wetland from the reservoir by a constant flow pump at a constant rate, and the treated water flows into the collecting basin from the uppermost outlet valve of the catchment area.
  • NaNO 3 was used as the nitrogen source
  • the concentration of NO 3 - -N was 12 mg/L
  • the fermentation liquid of valerian was used as the carbon source.
  • the influent COD/N was changed to 0, 8, 16 , and 24 by changing the amount of yarrow fermentation broth.
  • the constant flow pump adjusts the water inlet rate so that the hydraulic retention time is 2, 4, and 8 hours.
  • the water was continuously infused and discharged for 2 days under each hydraulic retention time, and water samples were taken every 8 hours to measure total nitrogen, nitrate nitrogen, ammonia nitrogen, nitrous nitrogen, total phosphorus, COD Cr , pH, and DO. The experiment was repeated three times.
  • Example 1 Preparation of fermented sludge.
  • the fermentation sludge used in the experiment was taken from the excess sludge after dewatering in a sewage treatment plant.
  • acclimation medium glucose 15g/L, NaNO 3 3.04g/L, KH 2 PO 4 0.44g/L, MgSO 4 ⁇ 7H 2 O0.96g/L, CaCl 2 0.72g/L, NaHCO 3 0.96 g/L, MnCl 2 0.11 g/L. Then, the excess sludge dehydrated in the 2.5kg sewage treatment plant was charged into a 5L fermenter, 4L domestication medium was added, the pH was adjusted to 7.4, and the temperature was adjusted at 28 °C for one week, and the pH was monitored daily.
  • the fermented sludge in the following examples was prepared in accordance with the above method.
  • Example 2 Preparation of valerian fermentation broth.
  • the alfalfa used in the experiment was collected from Tianzhu River, Xianlin Campus, Nanjing University. After the grass is collected, drain and weigh 1.3kg.
  • the fan machine was crushed and placed in a fermenter having a volume of 5 L, and 350 ml of the domesticated fermentation sludge and 3000 ml of tap water were added to adjust the pH to 7-8.
  • the fermenter was placed in a water-tight constant temperature incubator, and anaerobic fermentation was carried out at 30 ° C for 7 days.
  • the fermentation broth was filtered to remove the valerian residue, and the filtrate was collected and stored at 4 ° C for use.
  • valerian fermentation broth in the following examples were prepared as described above.
  • Example 3 Effect of adding valerian fermentation broth on denitrification effect of constructed wetland.
  • the mashed fermentation broth was added as the additional carbon source of the horizontal subsurface flow constructed wetland.
  • the effluent water quality was shown in Table 2 under different influent COD/N and different hydraulic retention time (HRT) conditions.
  • Example 4 Effect of adding valerian fermentation broth on effluent NH 3 -N, TP.
  • the sorghum fermentation broth was added as an additional carbon source for the horizontal subsurface flow constructed wetland.
  • the results of the effluent NH 3 -N and TP are shown in Table 2.
  • Figures 3 and 4 respectively reflect the removal effects of NH 3 -N and NH 3 -N by the horizontal subsurface flow constructed wetland system.
  • concentration of NH 3 -N and TP in the effluent increased with the increase of COD/N in the influent. This is mainly because the higher the influent COD/N, the nitrogen (mainly ammonia nitrogen) brought in by the addition of the alfalfa fermentation broth. The more phosphorus there is. It can be seen from Fig. 3 and Fig. 4 that there is no significant correlation between the NH 3 -N and TP removal rates and the influent COD/N, but both increase with the extension of the hydraulic retention time.
  • the nitrogen and phosphorus added by the fermentation liquid can be removed by the system itself without affecting the effluent quality.

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Abstract

本发明公开了一种菹草发酵液在人工湿地脱氮中的应用。按照如下方法制备菹草发酵液：菹草收集后沥干，粉碎，然后将粉碎后的菹草置于发酵罐中，与经过驯化的发酵污泥混合，再加入水，恒温发酵，去除菹草残渣，制备得到菹草发酵液。本发明还公布了上述菹草发酵液在人工湿地脱氮中的应用。该方法具有操作简单、原料廉价易得、脱氮效果好等优点，具有重要的社会、经济、生态效益。

Description

一种菹草发酵液在人工湿地脱氮中的应用 技术领域
本发明属于环境工程领域，具体涉及一种菹草发酵液在人工湿地脱氮中的应用。
背景技术
近年来，太湖流域河流水质全年综合评价结果显示，85.2％的监测断面水质无法达到Ⅲ类要求，大部分为Ⅴ类和劣Ⅴ类。其中主要的超标污染物为氨氮、高锰酸盐指数、溶解氧、五日生化需氧量、石油类、总磷和化学需氧量。上游入湖河流和湖荡地区水质持续恶化直接导致太湖入湖污染物总量不断增加。受入湖污染物增加的影响，太湖水体中的TP、TN含量在近年来基本呈持续上升趋势。因此，保护太湖水环境的关键是从源头将进入太湖的污染物截留，重点控制入湖河流排入湖区的污染物总量。
目前，太湖流域共有城镇污水处理厂近200座，均执行《城镇污水处理厂污染物排放标准》(GB18918-2002)中的一级A排放标准。但一级A排放标准(TN 15mg/L，NH3-N 5(8)mg/L，TP 0.5mg/L)仍然是大大超过地表水环境质量标准(地表水Ⅴ类水标准TN 2mg/L，NH3-N 2mg/L，TP 0.4(湖泊0.2)mg/L)。面对太湖水体富营养化日趋严重的现状，大量排放的污水处理厂尾水若不经过深度处理直接排放，将对入湖河道的水质产生极大影响，继而加剧太湖水体氮、磷污染程度，威胁饮用水安全。同时，对尾水进行深度处理、回用也是解决太湖流域水资源短缺、开辟第二水资源、减少新鲜水用量的有力措施，是城市可持续发展的必然要求，具有显著的环境、经济和社会效益。
目前常用的污水处理厂尾水深度处理技术主要有物化法(过滤法、吸附法等)、生物法(生物反应器、生物滤池、人工湿地等)和膜分离法(反渗透、微滤、纳滤等)，其中人工湿地技术因其投资和维护费用低、氮磷去除效果好、二次污染小且兼具景观效果等优点而被广泛应用。
对污水厂尾水进行水质分析，发现其氮素高度硝化、碳源严重不足。调查还显示，太湖流域的城镇污水厂中有将近50％的污水处理厂进水碳源不足。而碳源是反硝化过程中的电子供体，是制约反硝化作用的关键因素，要实现污水厂尾水的深度处理，必须添加足够的外加碳源，保证一定的碳氮比才能使反硝化过程顺利完成。
传统的反硝化外加碳源以液态有机物为主，包括葡萄糖、甲醇、乙醇和乙酸等。但 脱氮成本高，且甲醇、乙醇、乙酸等碳源有一定毒性，会对环境造成潜在危险。近年来，国内外许多研究者通过多种途径寻找低毒、廉价的新型碳源来代替传统碳源。
人工湿地中种植了大量富含纤维素类物质的水生植物，这些植物在冬季收割后经过厌氧发酵可以产生大量挥发性脂肪酸(VFAs)和其他营养元素，是优良的潜在外加碳源。
以人工湿地中大量种植的水生植物为原料，通过厌氧发酵将植物体中富含的纤维素类物质转化为挥发性脂肪酸(VFAs)和其他营养元素，作为反硝化外加碳源，实现污水厂尾水的深度脱氮处理，同时可解决人工湿地植物收割后的处置问题，实现水生植物的资源化利用，重要的研究意义和应用价值。
已有的研究结果表明，微生物的硝化反硝化作用是自然界氮素循环的重要途径之一。反硝化作用是在无氧或低氧条件下，微生物将硝态氮和亚硝态氮转化成氮气并释放到大气中的过程。反硝化脱氮的主要影响因素有溶解氧(DO)、pH、温度、碳源等。
(1)溶解氧(DO)一般认为，溶解氧保持在0.5mg/L以下时，反硝化作用才能正常进行。这是因为O2接受电子的能力高于NO2 --N和NO3 --N，当同时存在分子态氧和硝酸盐时，反硝化细菌优先进行有氧呼吸。
(2)pH反硝化作用的最佳pH是7～8。
(3)温度反硝化作用的最佳温度是15～30℃。对于温度的降低，反硝化细菌比硝化细菌更加敏感。当出现季节性降温时，反硝化过程将先于硝化过程而受到抑制，此时需要外加碳源来改善脱氮效果。此外，温度对微生物活性也会产生显著影响，进而影响反效果效果。
(4)碳源碳源是反硝化过程中的电子供体，同时也是微生物生长和繁殖所需能量的主要来源。碳源不足将直接影响反硝化作用，添加外加碳源是提高反硝化脱氮效率的有效方法之一。外加碳源的种类和投加量均会对反硝化效率产生显著影响。
现有的外加碳源大体可以分为两类，即传统碳源和新型碳源。传统碳源以液态有机物为主，包括低分子有机物类(如甲醇、乙醇和乙酸等)和糖类物质(如葡萄糖、蔗糖等)。新型碳源主要包括富含纤维素类物质的天然固体有机物(如植物秸秆等)、一些可降解的人工材料(如废纸、可降解餐盒等)以及高含碳量的工业废水等。
甲醇、乙醇、乙酸等低分子有机物因分子小、易被反硝化菌利用而被认为是理想的外加碳源。Gersberg等(1983)通过添加甲醇使人工湿地系统脱氮效率达到95％。Pochana 等(1999)的研究结果表明，添加乙酸为碳源可以大大提高同步硝化反硝化的进程。Rustige等(2007)在复合流人工湿地的水平流段添加乙酸作为碳源处理垃圾渗滤液，结果表明反硝化速率随着乙酸添加量的增加而增大，硝酸盐去除率最高可达98％。该类碳源脱氮效率虽然高，但是存在价格昂贵、运营成本高等缺点，且甲醇具有一定毒性、运输不便。
糖类物质作为外加碳源，处理效果较好，成本也较低。赵联芳等(2006)以人工湿地处理城市污染河水，对于硝氮浓度高的污水，通过添加葡萄糖可以有效提高除氮效果，湿地C/N由2提高至8时，TN去除率由55％提供至89％。佘丽华等(2009)通过复合垂直流人工湿地(IVCW)系统特有的通气管补充碳源到湿地底部强化湿地脱氮效果，结果表明，葡萄糖作为外加碳源时的脱氮效果优于羧甲基纤维素(CMC)，对于处理量60L/d的IVCW系统最佳葡萄糖投加量为1.5g，葡萄糖与硝氮的质量比仅为4.3，投加量远低于反硝化所需的C/N。但是葡萄糖作碳源时，微生物细胞产率高，容易导致人工湿地等工艺出现堵塞现象。
刘刚等(2010)认为，以工业废水作为外加碳源时反硝化效率受到工业废水中低分子有机物含量的限制，如果废水中低分子有机物含量低，反硝化效率就不会得到明显提高。同时废水投加过程中必须控制投加比例，防止出水水质恶化。
纤维素类碳源来源广泛、成本低廉，目前研究的富含纤维素类物质的固体有机碳源有废纸、玉米秸秆、麦秆、稻草以及香蒲、芦苇等水生植物枝条或茎秆等。文辉等(2011)研究了以麦秆作为外加碳源时对模拟人工湿地脱氮效果的促进作用，结果表明进水硝氮浓度为30mg/L时，去除硝氮最优条件是温度25℃，反应时间10h，麦秆与水的质量比为1:50。扫描店电镜结果显示，反应过的麦秆表面出现了空洞，由致密的横纹结构变为破裂的丝状结构，表明麦秆表面的可生物降解成分被微生物大量分解作为了反硝化的碳源。金赞芳等(2004)研究了棉花和纸作为碳源时的脱氮效果，结果显示这两种碳源均能使反应器快速启动，在室温25℃，进水硝氮分别为22.6、45.2mg/L，水力停留时间分别为9.8、8.6h时，硝氮去除率分别可达到100％、99.6％，且出水无亚硝氮累积。陈云峰等(2010)比较了麦秆、花生壳、红薯干、玉米芯、美人蕉枯叶、可降解餐盒、聚丁二酸丁二醇酯(PBS)和聚羟基脂肪酸酯(PHAs)作为碳源时的反硝化效果，优选出麦秆更适合作为污水处理厂尾水反硝化补充碳源。赵连芳等(2009)根据玉米秸秆、稻壳、木屑及芦苇杆这4种富含有机质的植物材料有机物释放规律及植物体分解水质的潜在影 响情况，确定芦苇竿为较适宜的植物碳源，当其添加量为1.0kg/m2时，垂直流人工湿地TN去除率由60％提高至80％。以纤维素类物质作为碳源不仅脱氮效果较好，价廉易得，且达到废物利用的目的，符合我国现阶段节能减排和循环经济的发展要求。但其缺陷是碳源的释放不能得到有效控制、需要的水力停留时间较长、出水水质易受外界温度影响。
城市有机废水(如酿酒废水、糖蜜废水、淀粉废水等)及城市污水厂剩余污泥中含有大量易生物降解物质，经厌氧发酵后能产生大量的短链挥发性脂肪酸，如乙酸、丙酸等，是优质的反硝化外加碳源，可以被反硝化微生物优先利用。表1总结了研究较多的城市有机废弃物厌氧产酸发酵液作为反硝化补充碳源时的脱氮效果。
表1 废弃生物质厌氧产酸发酵液作为反硝化碳源研究概况
Figure PCTCN2014094197-appb-000001
目前国内外学者研究较多的是利用城镇污水厂剩余污泥厌氧发酵酸化产物作为外加碳源时的脱氮效果。以剩余污泥作为发酵底物，既减少了污泥量，降低了污泥的处理成本，又为污水脱氮除磷提供了优质碳源，降低了碳源成本。佟娟(2008)以剩余污泥在碱性条件下得到的发酵液作为补充碳源处理低COD的生活污水，并以实际污水作为碳源进行对比研究，结果表明添加发酵液后SBR的脱氮除磷效果得到大大提升，COD、TN和SOP的去除率分别达到93％、80.9％和97.2％，而添加实际污水作碳源时COD、TN和SOP的去除率分别只有85％、63.5％和43.9％。刘道广采用表面活性剂促进污泥发酵产酸，以发酵液作为脱氮除磷系统的碳源，TP、NH3-N和TN的去除率分别达到97％、95％和81％，发酵液中VFAs被利用的顺序为丁酸、丙酸、乙酸。
菹草生命力强、适应力广，因而在人工湿地中得到大量种植。菹草富含纤维素类物质，收割后经过厌氧发酵可以产生大量挥发性脂肪酸(VFAs)和其他营养元素，是优良的潜在外加碳源，可作为反硝化的碳源供给，实现污水厂尾水的潜流式人工湿地深度脱氮处理，同时可解决人工湿地植物收割后的处置问题，实现水生植物的资源化利用。
发明内容
本发明所要解决的技术问题是提供菹草发酵液作为碳源，添加到人工湿地中，对污水进行脱氮处理的应用。
为解决上述技术问题，本发明所采用的技术方案如下：
一种菹草发酵液在人工湿地脱氮中的应用。
其中，所述的菹草发酵液按如下方法制备得到：
(1)菹草的准备：菹草收集后用水洗净，沥干，粉碎；
(2)发酵液的制备：将粉碎后的菹草置于发酵罐中，与经过驯化的活性污泥混合，再加入去除了溶解氧的水，恒温发酵，过滤去除菹草残渣，制备得到菹草发酵液。
其中，步骤(2)中，菹草、活性污泥以及水按100kg:1L：1L比例投放。
步骤(2)中，活性污泥的驯化方法采用本领域公知的方法培养驯化，通过控制驯化培养基的成分和驯化温度、pH、时间，最终使反硝化微生物成为优势菌群；优选采用如下方法驯化：
驯化培养基的组成如下：葡萄糖15g/L、NaNO33.04g/L、KH2PO40.44g/L、MgSO4·7H2O0.96g/L、CaCl20.72g/L、NaHCO30.96g/L、MnCl20.11g/L。
将2.5kg污水处理厂脱水后的剩余污泥装入5L的发酵罐中，加入4L驯化培养基，调节pH为7.4，28℃驯化一周，每天监测pH。
其中，步骤(2)中，发酵温度为12-30℃，优选为20-30℃，最优选为30℃。
其中，发酵的时间为5-10天，优选为7天。
其中，发酵过程中的pH控制为7～8，优选为7～7.5。
其中，污水为污水处理厂尾水，其中氮的含量为10-15mg/L，优选为12mg/L。
其中，将菹草发酵液按照如下添加量计算投加入污水：菹草发酵液的COD值与污水中的N含量的比值为8-16，优选为9-10；同时尾水的水力停留时间为4-8h，优选为6h。
有益效果：
本发明具有如下显著特点和效果：
1、菹草原料来源广、成本低，制备菹草发酵液方法简单易行。
2、将菹草再次资源化利用，解决了菹草收割后难处理的问题，减轻了其对环境的危害。
3、将菹草发酵液作为碳源添加到污水尾水处理的人工湿地中，能够快速有效地提高潜流式人工湿地的脱氮效率，且随发酵液添加带入的氮磷不会影响出水水质。
附图说明
图1水平潜流式人工湿地装置图；
图2潜流式人工湿地TN去除率；
图3潜流式人工湿地NO3 --N去除率；
图4潜流式人工湿地NH3-N去除率；
图5潜流式人工湿地TP去除率。
具体实施方式
根据下述实施例，可以更好地理解本发明。然而，本领域的技术人员容易理解，实施例所描述的内容仅用于说明本发明，而不应当也不会限制权利要求书中所详细描述的本发明。
实施例中所用的实验装置其结构如图1所示。该实验装置为水平潜流式人工湿地，由PVC有机玻璃板制成，内径长×宽×高＝40cm×15cm×30cm，分布水区、处理区和集水区三部分。布水区长5cm，宽15cm，通过穿孔板与处理区隔开，穿孔板由下至上均匀分布4个直径为2cm的圆形过水孔，区内铺设粒径为3cm的砾石，对进水初步过滤，以防止湿地内部堵塞。处理区长30cm，宽15cm，填充25cm厚的混有蛭石的土壤(蛭石与土壤混合质量比例为1:1，蛭石粒径为1cm)，区内种植菖蒲6株，菖蒲采自南京大学仙林校区天籁河，植株高约50～60cm，生长旺盛。集水区长5cm，宽15cm，通过穿孔板与处理区隔开，区内铺设粒径为3cm的砾石。出水阀有3个，分别设在0cm、10cm、25cm高度，以调节水位。
实施例中所用到的仪器有：保定兰格BT-2型恒流泵，XX型磁力搅拌器，1.5L抽 滤瓶，1.25L哇哈哈纯净水瓶，植物粉碎机，隔水式恒温培养箱，紫外-可见分光光度计UV2450，D-1型自动蒸汽灭菌锅，电子天平，25mL具塞玻璃磨口比色管，石英比色皿，超纯水系统(Milli-Q，Millipore)，0.45μm水系滤膜。
实施例出水和进水的组分的检测方法如下：(1)TN测定采用过硫酸钾氧化-紫外分光光度法：(2)NO3 --N测定采用紫外分光光度法；(3)NO2 --N测定N-(1-萘基)-乙二胺光度法；(4)NH3-N测定采用纳氏试剂光度法：(5)TP测定采用过硫酸钾消解-钼酸铵显色法：CODCr测定采用重铬酸钾法：(6)DO测定采用哈希HQ30d便携式溶氧仪；(7)pH测定采用哈希HQ30d便携式pH计。
在进行正式试验前，需对人工湿地系统进行调试。系统于2013年8月中旬启动，在前3次进水中添加一定量以反硝化培养基驯化后的活性污泥，进行微生物接种，进水以NaNO3为氮源，葡萄糖为碳源，进水硝氮浓度为15mg/L，C/N设为8，运行1个月后出水水质稳定，4套湿地装置均达到稳定运行状态，且相同条件下的脱氮效率无显著差异。
进水由恒流泵自储水池以恒定速率抽入人工湿地的布水区，处理后的水由集水区最上端出水阀流入集水池。以NaNO3为氮源，NO3 --N浓度12mg/L，菹草发酵液为碳源，通过改变菹草发酵液添加量使进水COD/N依次为0、8、16、24，通过恒流泵调节进水速率使水力停留时间为2、4、8h。每个水力停留时间下连续进出水2d，每隔8h取出水水样，测定总氮、硝氮、氨氮、亚硝氮、总磷、CODCr、pH、DO。实验重复3次。
实施例1：发酵污泥的制备。
实验所用发酵污泥取自某污水处理厂脱水后的剩余污泥。
以下组分配制驯化培养基：葡萄糖15g/L、NaNO33.04g/L、KH2PO40.44g/L、MgSO4·7H2O0.96g/L、CaCl20.72g/L、NaHCO30.96g/L、MnCl20.11g/L。再将2.5kg污水处理厂脱水后的剩余污泥装入5L的发酵罐中，加入4L驯化培养基，调节pH为7.4，28℃驯化一周，每天监测调控pH。
以下实施例中的发酵污泥均按照上述方法制备。
实施例2：菹草发酵液的制备。
实验所用菹草采自南京大学仙林校区天籁河。菹草采集后沥干，称取1.3kg，用植 物粉丝机粉碎，置于体积为5L的发酵罐中，同时加入驯化后的发酵污泥350ml，以及自来水3000ml，调节pH为7-8。发酵罐置于隔水式恒温培养箱中，30℃厌氧发酵7天，发酵液过滤除去菹草残渣，收集滤液，4℃保存备用。
以下实施例中的菹草发酵液均按照上述方法制备。
实施例3：添加菹草发酵液对人工湿地脱氮效果的影响。
添加菹草发酵液作为水平潜流式人工湿地的外加碳源，不同进水COD/N、不同水力停留时间(HRT)条件下，出水水质如表2所示。
由图1、2可知，3种水力停留时间下，TN、NO3 --N去除率均随进水COD/N值增大而提高。进水COD/N＝0即未添加菹草发酵液时，3种水力停留时间下TN、NO3 --N去除率分别为4％～9％、4％～14％，说明此时反硝化脱氮效率很低；进水COD/N＝8时，TN、NO3 --N去除率分别提高至37％～74％、68％～87％，系统脱氮效率较未添加菹草发酵液时显著提升(p＝0.001)；继续提高进水COD/N＝16、20时，TN、NO3 --N去除率分别达到66％～90％、84％～100％，系统反硝化作用强烈，出水NO3 --N浓度(HRT＝4、8h)低于检测限，出水NO2 --N未出现累积，说明此时菹草发酵液的添加量足够反硝化微生物实现完全反硝化。
比较相同进水COD/N、不同水力停留时间条件下的TN、NO3 --N去除率，发现TN、NO3 --N去除率随着水力停留时间的延长而升高。以进水COD/N＝16为例，HRT＝2、4、8h时，TN去除率分别为66％、80％、90％，NO3 --N去除率分别为84％、100％、100％，说明在碳源充足时，水力停留时间对出水氮含量有重要影响，适当延长水力停留时间有助于反硝化微生物去除更多的氮。
由表2可知，进水COD/N和水力停留时间均对出水NO2 --N含量有重要影响。进水COD/N＝8条件下，HRT＝2、4、8h时，出水NO2 --N浓度分别为4.1、2.1、0.35mg/L，分别较进水累积了205、105、17.5倍，这是因为此时碳源不足，反硝化过程停留在NO3 --N转化为NO2 --N的阶段，致使系统中NO2 --N不断累积。在提高进水COD/N＝16后，出水NO2 --N含量显著降低，累积程度极大减弱。同时发现出水NO2 --N浓度会随着水力停留时间的延长而降低，以进水COD/N＝16为例，HRT＝2、4、8h时，出水NO2 --N浓度分别为1.3、0.08、0.02mg/L，说明碳源充足时反硝化脱氮的NO2 --N转化为N2的过程主要发生在2～4h。
实施例4：添加菹草发酵液对出水NH3-N、TP的影响。
添加菹草发酵液作为水平潜流式人工湿地的外加碳源，出水NH3-N、TP结果如表2所示。
表2 人工湿地出水水质
Figure PCTCN2014094197-appb-000002
图3、4分别反映了水平潜流式人工湿地系统对NH3-N和NH3-N的去除效果。出水NH3-N、TP浓度均随着进水COD/N值得提高而增大，这主要是因为进水COD/N越高，随添加菹草发酵液带入的氮(主要是氨氮)、磷就越多。由图3、图4可知，NH3-N、TP去除率与进水COD/N之间无明显相关性，但均随水力停留时间的延长而升高。已有的研究表明，人工湿地系统中NH3-N的去除主要有3个途径：(1)湿地表面水体的氨氮通过挥发进入大气；(2)氨氧化细菌和氨氧化古菌将氨氮转化为硝氮，再通过反硝化作用转为N2；(3)植物吸收和基质吸附。人工湿地系统中磷的去除主要靠土壤的吸附作用。适当延长水力停留时间，可以使氨氧化细菌和氨氧化古菌有更多的时间转化氨氮，同时土壤吸附的氨氮、磷也更多。进水COD/N＝16、HRT＝4h时，人工湿地系统出水TP 含量为0.48mg/L，已接近地表水Ⅴ类水标准。
根据以上分析可知，HRT＝4h时，只要进水碳源充足，人工湿地系统中的反硝化微生物可以将进水NO3 --N完全去除，此时COD消耗量/N＝9.6，即为最佳进水COD/N。在最佳进水COD/N＝9.6时出水氨氮、TP含量完全可达到地表水Ⅴ类水标准，添加发酵液带入的氮磷可以被系统自身去除，不会影响出水水质。

Claims (8)

  1. 一种菹草发酵液在人工湿地脱氮中的应用。
  2. 根据权利要求1所述的应用，其特征在于，所述的菹草发酵液按如下方法制备得到：
    (1)菹草的准备：菹草收集后沥干，粉碎；
    (2)发酵液的制备：将粉碎后的菹草置于发酵罐中，与经过驯化的发酵污泥混合，再加入水，恒温发酵，去除菹草残渣，制备得到菹草发酵液。
  3. 根据权利要求2所述的菹草发酵液制备方法，其特征在于，步骤(2)中，菹草、活性污泥以及水按100kg:1L：1L比例投放。
  4. 根据权利要求2所述的菹草发酵液制备方法，其特征在于，步骤(2)中，发酵温度为12-30℃。
  5. 根据权利要求2所述的菹草发酵液的制备方法，其特征在于，步骤(2)中，发酵的时间为5-10天。
  6. 根据权利要求2所述的菹草发酵液的制备方法，其特征在于，步骤(2)中，发酵过程中pH控制为7～8。
  7. 根据权利要求1所述的应用，其特征在于，污水为污水处理厂尾水，其中氮的含量为10-15mg/L。
  8. 根据权利要求1所述的应用，其特征在于，将菹草发酵液按照如下添加量计算投加入污水处理厂尾水：菹草发酵液的COD值与尾水中的N含量的比值为8-16；尾水的水力停留时间为4-8h。
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Cited By (1)

* Cited by examiner, † Cited by third party
Publication number Priority date Publication date Assignee Title
CN118908421A (zh) * 2024-08-02 2024-11-08 铜陵学院 一种利用改性玉米芯强化水平潜流人工湿地脱氮除磷的方法

Families Citing this family (19)

* Cited by examiner, † Cited by third party
Publication number Priority date Publication date Assignee Title
CN104118943B (zh) * 2014-08-06 2016-02-10 南京大学 一种菹草发酵液在人工湿地脱氮中的应用
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US10584046B2 (en) * 2015-10-28 2020-03-10 Kaneka Corporation Nitrogen removal method, nitrification-reaction promoting agent for water treatment, and water treatment method
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Citations (7)

* Cited by examiner, † Cited by third party
Publication number Priority date Publication date Assignee Title
CN101492206A (zh) * 2009-03-09 2009-07-29 合肥工业大学 利用玉米秸秆原位修复地下水硝酸盐污染的方法
EP2093196A1 (en) * 2008-02-19 2009-08-26 Erik Meers Treatment of liquid dispersions of organic material to dischargeable / re-usable water
CN102174580A (zh) * 2011-02-10 2011-09-07 中国科学院过程工程研究所 一种水解酸化生物质原料制备发酵碳源的方法
CN102701450A (zh) * 2012-05-15 2012-10-03 上海师范大学 一种利用废弃植物落叶修复地表水的方法
CN104118937A (zh) * 2014-08-06 2014-10-29 南京大学 一种菹草发酵液在提高污水处理反硝化脱氮能力中的应用
CN104118943A (zh) * 2014-08-06 2014-10-29 南京大学 一种菹草发酵液在人工湿地脱氮中的应用
CN104131039A (zh) * 2014-08-06 2014-11-05 南京大学 一种水生植物厌氧发酵产有机酸的方法

Family Cites Families (1)

* Cited by examiner, † Cited by third party
Publication number Priority date Publication date Assignee Title
CN1769198B (zh) * 2005-09-05 2012-07-11 中国科学院生态环境研究中心 一种利用黏土凝聚将水华转化为水底植被的方法

Patent Citations (7)

* Cited by examiner, † Cited by third party
Publication number Priority date Publication date Assignee Title
EP2093196A1 (en) * 2008-02-19 2009-08-26 Erik Meers Treatment of liquid dispersions of organic material to dischargeable / re-usable water
CN101492206A (zh) * 2009-03-09 2009-07-29 合肥工业大学 利用玉米秸秆原位修复地下水硝酸盐污染的方法
CN102174580A (zh) * 2011-02-10 2011-09-07 中国科学院过程工程研究所 一种水解酸化生物质原料制备发酵碳源的方法
CN102701450A (zh) * 2012-05-15 2012-10-03 上海师范大学 一种利用废弃植物落叶修复地表水的方法
CN104118937A (zh) * 2014-08-06 2014-10-29 南京大学 一种菹草发酵液在提高污水处理反硝化脱氮能力中的应用
CN104118943A (zh) * 2014-08-06 2014-10-29 南京大学 一种菹草发酵液在人工湿地脱氮中的应用
CN104131039A (zh) * 2014-08-06 2014-11-05 南京大学 一种水生植物厌氧发酵产有机酸的方法

Cited By (1)

* Cited by examiner, † Cited by third party
Publication number Priority date Publication date Assignee Title
CN118908421A (zh) * 2024-08-02 2024-11-08 铜陵学院 一种利用改性玉米芯强化水平潜流人工湿地脱氮除磷的方法

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