Water source denitrification ecological reaction cabin double-membrane micro-ecological system as well as construction method and application thereof

Abstract

The invention relates to the technical field of environmental water treatment, and particularly discloses a double-membrane micro-ecological system of a water source denitrification ecological reaction cabin as well as a construction method and application of the double-membrane micro-ecological system. Comprising the following steps: adding an inorganic electron donor filler into a reactor, realizing alternation of aerobic / anaerobic environments through intermittent aeration, introducing reservoir source water into the reactor filled with the inorganic electron donor filler by adopting intermittent water feeding, and repeating the step of intermittent water feeding for 3-5 times until an aerobic denitrification enhanced nitrogen removal part is formed on the surface of the inorganic electron donor. According to the constructed double-membrane micro-ecological system of the denitrification ecological reaction chamber, the concentration of nitrogen pollutants and COD pollutants in micro-polluted water is effectively reduced, the problem of efficiency reduction caused by insufficient electron donors in the water is solved, and the practical requirement of micro-polluted water treatment is met.

Description

Technical Field

[0001] The invention relates to the technical field of environmental water treatment, and in particular to a double-membrane micro-ecological system in a water source denitrification ecological reaction chamber and a construction method and application thereof. Background Art

[0002] With the acceleration of industrialization and urbanization, the concentration of nitrogen pollutants and chemical oxygen demand pollutants in water bodies is increasing, which not only causes serious damage to aquatic ecosystems, but also poses a potential threat to human health. Based on the current research status of lake and reservoir water pollution, the pollution state of most lake and reservoir water bodies is micro-polluted, and the concentration of pollutants is low, but the impact on the aquatic ecosystem cannot be ignored. In the field of environmental water treatment technology, especially for water purification problems in water source reservoirs, traditional treatment methods often face certain limitations, such as physical sedimentation, chemical flocculation, etc. Although some pollutants can be removed to a certain extent, there are often problems such as low treatment efficiency, high cost, and secondary pollution. In terms of biological treatment, due to the lack of electron donors in micro-polluted water bodies, traditional biological treatment methods often find it difficult to achieve ideal treatment effects, resulting in reduced treatment efficiency.

[0003] At present, there are few technical research and developments at home and abroad on achieving efficient denitrification by enhancing the activity of indigenous aerobic denitrifying bacteria in slightly polluted water bodies. When treating low carbon-nitrogen ratio water sources, additional organic carbon sources may lead to secondary pollution risks and increase treatment costs. At present, the treatment of slightly polluted water bodies is mainly through oxygenating the water bodies. However, oxygenation can only inhibit the anaerobic release of nutrients in water sediments and cannot fundamentally achieve the purpose of improving water quality. Therefore, it is urgent to propose an environmentally friendly method to improve the water quality of lake and reservoir water sources. Summary of the invention

[0004] In order to develop an environmentally friendly method for improving the water quality of lake and reservoir water sources, the present invention provides a water source denitrification ecological reaction chamber double membrane micro-ecological system and its construction method and application. The denitrification denitrification ecological reaction chamber double membrane micro-ecological system constructed by the method provided by the present invention effectively reduces the concentration of nitrogen pollutants and COD pollutants in micro-polluted water bodies, solves the problem of efficiency reduction caused by insufficient electron donors in water bodies, and meets the practical requirements of micro-polluted water body treatment.

[0005] The present invention provides a method for constructing a double-membrane micro-ecological system of a denitrification and denitrification ecological reaction chamber, comprising the following steps: Inorganic electron donor fillers with a volume fraction of 10% to 40% are added to the reactor, and an aerobic / anaerobic alternating environment is created through intermittent aeration. During the intermittent aeration process, the ratio of aeration time to interval time is 10 h to 12 h:12 h. Reservoir source water is introduced by intermittent water inflow. During the intermittent water inflow, the hydraulic retention time in the reactor is 3 d to 7 d, and the water inflow time is 1 h to 2 h. The intermittent water inflow step is repeated 3 to 5 times until an aerobic denitrification enhanced denitrification part is generated on the surface of the inorganic electron donor filler, and a double-membrane micro-ecological system of the denitrification denitrification ecological reaction chamber is obtained.

[0006] The invention uses a method for constructing a double-membrane micro-ecological system of a denitrification denitrification ecological reaction chamber to generate an aerobic denitrification enhanced denitrification part on the surface of an inorganic electron donor filler, thereby obtaining a double-membrane micro-ecological system of a denitrification denitrification ecological reaction chamber. The double-membrane micro-ecological system of the ecological reaction chamber is coupled with an inorganic electron donor enhanced denitrification by an aerobic denitrification microbial membrane in the aerobic denitrification enhanced denitrification part, thereby effectively reducing the content of total nitrogen, nitrate, nitrite and ammonia in the water environment.

[0007] The present invention also provides a double-membrane micro-ecological system of a denitrification and denitrification ecological reaction chamber constructed by the construction method, comprising an inorganic electron donor and an aerobic denitrification enhanced denitrification part formed on its surface.

[0008] The present invention also provides an application of the double-membrane micro-ecological system of the denitrification denitrification ecological reaction chamber in water treatment. The double-membrane micro-ecological system of the denitrification denitrification ecological reaction chamber is used for denitrification of water bodies in water source reservoirs.

[0009] Compared with the prior art, the present invention has the following beneficial effects: The construction method provided by the present invention combines inorganic electron donors to strengthen indigenous bacterial colonies, creates an aerobic / anaerobic alternating environment through intermittent aeration, and pumps the water body to circulate at a low speed to fully contact and react with the filler, so that it forms an ecological reaction chamber double-membrane micro-ecological system on the surface of the inorganic electron donor filler. The water source denitrification ecological reaction chamber double-membrane micro-ecological system includes an inorganic electron donor and an aerobic denitrification enhanced denitrification part formed on its surface. The water source denitrification ecological reaction chamber double-membrane micro-ecological system is divided into an inner layer and an outer layer, the inner layer is an anaerobic / facultative anaerobic autotrophic microorganism inorganic electron donor reduction part, and the inorganic electron donor is reduced by metal-reducing bacteria and the electrons are transferred to the outer layer; the outer layer is an aerobic denitrification enhanced denitrification part, and the indigenous aerobic denitrifying bacteria receive the electrons provided by the inner layer to perform denitrification function denitrification, and oxidize nitrate in the water body to nitrogen gas for nitrogen removal, which solves the defect of lacking sufficient electron donors in micro-polluted water bodies, can effectively improve the removal efficiency of nitrogen and COD pollutants in water bodies, and meet the practical requirements of micro-polluted water body treatment.

[0010] The inorganic electron donor filler of the present invention is made of a certain mass of metal or its compound, and the metal provides electrons for the reaction system, solves the defect of insufficient electron donor of organic carbon in source water, and improves the denitrification capacity of in-situ denitrifying bacteria. In addition, the required metal and inorganic carbon have low economic cost, no secondary pollution, and have broad application potential.

[0011] The present invention is suitable for the treatment of various micro-polluted water bodies by constructing a specific micro-ecological system, and promotes the diversity and ecological balance of microorganisms in the water body, reduces the use of chemical reagents, reduces secondary pollution to the environment, and promotes the long-term health of the water body. The micro-ecological system is cultivated through intermittent aeration and low-speed circulation of the pump, is simple to operate, easy to realize automatic control, suitable for large-scale application, meets the practical requirements of micro-polluted water body treatment, and has strong adaptability and broad application prospects. BRIEF DESCRIPTION OF THE DRAWINGS

[0012] In order to more clearly illustrate the embodiments of the present invention or the technical solutions in the prior art, the drawings required for use in the embodiments or the description of the prior art will be briefly introduced below. Obviously, the drawings described below are only some embodiments of the present invention. For ordinary technicians in this field, other drawings can be obtained based on these drawings without paying creative work.

[0013] Figure 1 This is a model diagram of a double-membrane micro-ecological system in a water source denitrification ecological reaction chamber according to Example 1 of the present invention.

[0014] Figure 2 This is a scanning electron microscope image of a double-membrane micro-ecological system of a water source denitrification ecological reaction chamber constructed by using iron as an inorganic electron donor filler in Example 2 of the present invention.

[0015] Figure 3 This is a scanning electron microscope image of a double-membrane micro-ecological system of a water source denitrification ecological reaction chamber constructed by using manganese as an inorganic electron donor filler in Example 2 of the present invention.

[0016] Figure 4 This is a graph showing the measurement results of the change in water nitrogen concentration and nitrogen removal rate of the double-membrane micro-ecological system reactor without denitrification ecological reaction chamber in two reaction cycles of the present invention.

[0017] Figure 5 The graph is a measurement result of the change of nitrogen concentration in the water body and the nitrogen removal rate in two reaction cycles of the double-membrane micro-ecological system of the water source denitrification ecological reaction chamber constructed by the present invention; In the figure, (a) shows the removal of nitrogen by the double-membrane micro-ecological system in the iron-based water source denitrification ecological reaction chamber. The left figure shows the change of nitrogen concentration at different times, and the right figure shows the change of nitrogen removal efficiency at different times. (b) The removal of nitrogen by the double membrane micro-ecosystem in the manganese-based water source denitrification ecological reaction chamber; (c) Shows the removal of nitrogen by the double-membrane micro-ecosystem in the iron-manganese composite water source denitrification ecological reaction chamber.

[0018] Figure 6 The COD of the water body in the double membrane micro-ecological system reactor of the water-free denitrification ecological reaction chamber in Example 3 of the present invention in two reaction cycles Mn Graph showing concentration changes and removal rate measurement results.

[0019] Figure 7 The COD of the water body in the double membrane micro-ecological system reactor containing the water source denitrification ecological reaction cabin in Example 3 of the present invention in two reaction cycles Mn Graph showing concentration changes and removal rate measurement results.

[0020] Figure 8 This is a graph showing the change in TP concentration in the water body and its removal rate measurement results of the double-membrane micro-ecological system reactor in the water-free denitrification ecological reaction chamber in Example 3 of the present invention during two reaction cycles.

[0021] Fig. 9 This is a graph showing the change in TP concentration in the water body and its removal rate measurement results of the double-membrane micro-ecological system reactor containing a water source denitrification ecological reaction chamber in Example 3 of the present invention during two reaction cycles.

[0022] Fig.10 This is a bar graph showing the measurement results of changes in total microbial ATP and ETSA concentrations in the double-membrane micro-ecological system reactor of the water source denitrification ecological reaction chamber in Example 4 of the present invention during two reaction cycles.

[0023] In the figure, (a) is the total ATP concentration of microorganisms in the reactor during two reaction cycles; (b) is the total ETSA concentration of microorganisms in the reactor during two reaction cycles.

[0024] Fig.11 This is a bar graph showing the results of measuring the relative activity changes of complex I and complex III in the water body of the double membrane micro-ecological system reactor for water source denitrification ecological reaction chamber in Example 4 of the present invention during two reaction cycles.

[0025] In the figure, (a) shows the relative activity of complex I in the water of the reactor during two reaction cycles; (b) The relative activity of complex III in the water of the reactor during two reaction cycles.

[0026] Fig.12 This is a bar graph showing the results of measuring the abundance of Nar and Nir enzymes in the water body of the double-membrane micro-ecological system reactor of the water source denitrification ecological reaction chamber in Example 4 of the present invention during two reaction cycles.

[0027] In the figure, (a) shows the abundance of Nir enzyme in the water of the reactor during two reaction cycles; (b) The abundance of Nar enzyme in the water of the reactor during two reaction cycles.

[0028] Fig.13 This is a bar graph showing the percentage of bacterial flora at the phylum level in the water body of the double membrane micro-ecological system reactor for water source denitrification ecological reaction chamber in Example 5 of the present invention during two reaction cycles.

[0029] In the figure, (a) shows the bacterial flora at the gate level in the water body of the reactor during two reaction cycles; (b) Phylum-level bacterial flora in the sediment of the reactor during two reaction cycles.

[0030] Fig.14 This is a heat map of the scientific level bacterial flora in the water body of the double membrane micro-ecosystem reactor of the water source denitrification ecological reaction chamber in Application Example 5 of the present invention during two reaction cycles.

[0031] In the figure, (a) shows the bacterial flora at the science level in the water of the reactor during two reaction cycles; (b) The family-level bacterial flora in the sediment of the reactor during two reaction cycles.

[0032] Fig.15 This is a graph showing the measurement results of the change in water nitrogen concentration and nitrogen removal rate of the double-membrane micro-ecological system reactor without denitrification ecological reaction chamber in the present invention during five reaction cycles.

[0033] Fig.16 The graph is a measurement result of the change of nitrogen concentration in the water body and the nitrogen removal rate of the double-membrane micro-ecological system of the denitrification denitrification ecological reaction chamber constructed by the present invention during five reaction cycles; In the figure, (a) shows the removal of nitrogen by the double-membrane micro-ecosystem in the manganese-based denitrification ecological reaction chamber; (b) shows the removal of nitrogen by the double-membrane micro-ecosystem in the composite manganese-based denitrification ecological reaction chamber; Fig.17 The COD of water in the double membrane micro-ecological system reactor without denitrification and denitrification ecological reaction chamber and the double membrane micro-ecological system reactor with denitrification and denitrification ecological reaction chamber in five reaction cycles Mn Concentration change and removal rate measurement results diagram; In the figure, (a) shows the effect of double membrane micro-ecological system on COD without denitrification denitrification ecological reaction chamber Mn removal of (b) The double membrane micro-ecological system of manganese-based denitrification ecological reaction chamber and the double membrane micro-ecological system of composite manganese-based denitrification ecological reaction chamber have an impact on COD Mn removal situation.

[0034] Fig.18 It is a graph showing the change of TP concentration in water and its removal rate in five reaction cycles of the double membrane micro-ecological system reactor without denitrification and denitrification ecological reaction chamber and the double membrane micro-ecological system reactor with denitrification and denitrification ecological reaction chamber in the present invention; In the figure, (a) shows the removal of TP by the double-membrane micro-ecosystem in the denitrification ecological reaction chamber without denitrification; (b) Shows the removal of TP by the double-membrane micro-ecosystem of the manganese-based denitrification ecological reaction chamber and the double-membrane micro-ecosystem of the composite manganese-based denitrification ecological reaction chamber. DETAILED DESCRIPTION

[0035] The specific embodiments of the present invention are described in detail below, but it should be understood that the protection scope of the present invention is not limited by the specific embodiments. Based on the embodiments in the present invention, all other embodiments obtained by ordinary technicians in this field without creative work belong to the scope of protection of the present invention. The experimental methods described in the embodiments of the present invention are conventional methods unless otherwise specified, and the materials, reagents, etc. used in the following embodiments can be obtained from commercial channels unless otherwise specified.

[0036] Example 1: Double membrane micro-ecological system of water source denitrification ecological reaction chamber and its construction method.

[0037] The reactor is filled with an inorganic electron donor filler, i.e., a filler containing an inorganic electron donor. The inorganic electron donor filler accounts for 40% of the volume fraction of the reactor, leaving a certain reserved space.

[0038] The reactor device is a columnar reactor made of transparent acrylic glass, the reactor volume is 5 L, and the size of the reactor is 130 mm inner diameter×376.7 mm column height. The inorganic electron donor filler is a metal iron filler, and the metal iron filler is iron powder.

[0039] After the inorganic electron donor filler is filled in the reactor, intermittent aeration is performed using an oxygenation pump. The aeration time and interval time ratio is set to 12 h:12 h, and the aeration rate is 15L gas / min / cubic meter to create an alternating aerobic / anaerobic environment to promote the growth of different types of bacteria. Intermittent water inlet is used to introduce reservoir source water, and a pump is used to push the water flow to circulate the source water at a low speed until the reactor is filled. The water flow is affected by resistance when passing through the filler, making the water flow velocity unevenly distributed, forming a circulation, promoting the contact between the filler and the water body, and increasing the impact on the water body. The hydraulic retention time in the reactor during the intermittent water inlet process is 5d, and the water inlet time is 2h each time. Repeat the water inlet 5 times, and the aerobic denitrification enhanced denitrification part is generated on the surface of the inorganic electron donor filler, that is, the iron-based water source denitrification ecological reaction chamber double membrane micro-ecological system is obtained.

[0040] The double-membrane micro-ecological system of the ecological reaction chamber includes: inner layer: anaerobic / facultative anaerobic autotrophic microorganisms inorganic electron donor reduction part, which reduces inorganic electron donors through metal-reducing bacteria and provides electrons to the outer layer; outer layer: aerobic denitrification enhanced denitrification part, indigenous aerobic denitrifying bacteria absorb the electrons provided by the inner layer for oxidation, thereby removing water pollutants and denitrifying.

[0041] Inorganic electron donors continuously provide electron donors for the indigenous aerobic denitrifying bacteria in the water body, enhancing the growth and denitrification capacity of the indigenous aerobic denitrifying bacteria. Ultimately, the obtained water source denitrification ecological reaction chamber double membrane micro-ecological system will be used for denitrification and removal of pollutants such as COD in water treatment water source reservoirs.

[0042] The source water is severely eutrophic lake reservoir source water, which comes from a reservoir in Yantai City, Shandong Province. The source water temperature is maintained above 10°C. The reservoir water provides the nutrients needed for its survival, and the aeration equipment oxygenation pump provides dissolved oxygen. It works intermittently with a cycle of 12 hours, releasing air into the reactor water body to form an air-water mixture in which tiny bubbles are in full contact with the water body, thereby achieving an overall alternating aerobic and anaerobic environment. At the same time, a pump is used to promote the low-speed circulation of water flow to provide the necessary conditions for the construction of a double-membrane micro-ecological system in the water source denitrification ecological reaction cabin. The metal filler provides an exogenous electron donor for the system. During the construction process, the metal filler is in full contact with the water body, so that the system can maintain its activity, generation renewal and denitrification capacity.

[0043] Table 1 Water quality parameters of a water source reservoir in Yantai

[0044] Example 2: Double membrane micro-ecological system of water source denitrification ecological reaction chamber and its construction method.

[0045] The water source denitrification ecological reaction chamber double membrane micro-ecological system provided in Example 2 is basically the same as that in Example 1, except that the inorganic electron donor filler accounts for 30% of the effective volume of the reactor. The inorganic electron donor filler is a metal manganese filler, and the metal manganese filler is manganese powder. The manganese-based water source denitrification ecological reaction chamber double membrane micro-ecological system is obtained according to the steps in Example 1.

[0046] Example 3: Double membrane micro-ecological system of water source denitrification ecological reaction chamber and its construction method.

[0047] The double-membrane micro-ecological system of the water source denitrification ecological reaction chamber provided in Example 3 is basically the same as that in Example 1, except that: the inorganic electron donor filler is a composite filler of metallic iron and inorganic carbon; the inorganic carbon is activated carbon. The preparation process of the composite filler of metallic iron and inorganic carbon is: wash the metallic iron twice with a 10% volume fraction H2SO4 solution, and then wash it once with deionized water to wash off the oxide coating on the surface; the activated carbon is granular, with a particle size of 16 mesh and a volume density of 0.75 g / m 3 , with a specific surface area of ​​285 m / g, and washed with distilled water three times before use; the activated carbon was dried and mixed with the washed metal iron at 25°C in an air-tight state, so that the metal iron powder adhered to the activated carbon to form a slow-release electron release system. The mass ratio of metal iron to activated carbon was 1:1.

[0048] According to the steps in Example 1, a composite iron-based water source denitrification ecological reaction chamber double membrane micro-ecological system is obtained.

[0049] Example 4: Double membrane micro-ecological system of water source denitrification ecological reaction chamber and its construction method.

[0050] The double membrane micro-ecological system of the water source denitrification ecological reaction chamber provided in Example 4 is basically the same as that in Example 1, except that: the inorganic electron donor filler accounts for 30% of the effective volume of the reactor, the inorganic electron donor filler is a composite filler of metal manganese and inorganic carbon; the inorganic carbon is activated carbon. The preparation process of the composite filler of metal manganese and inorganic carbon is: wash the metal manganese twice with a H2SO4 solution with a volume fraction of 10%, and then wash it once with deionized water to wash off the oxide coating on the surface; the activated carbon is granular, with a particle size of 16 mesh, and a volume density of 0.75 g / m 3 , with a specific surface area of ​​285 m / g, and washed with distilled water three times before use; the activated carbon was dried and mixed with the washed mineral at 25°C in an air-tight condition, so that the metal manganese powder adhered to the activated carbon to form a slow-release electron release system. The mass ratio of metal manganese to activated carbon was 1:1.

[0051] According to the steps in Example 1, a composite manganese-based water source denitrification ecological reaction chamber double membrane micro-ecological system is obtained.

[0052] Example 5: Double membrane micro-ecological system of water source denitrification ecological reaction chamber and its construction method.

[0053] The double-membrane microecological system of the water source denitrification ecological reaction cabin provided in Example 5 is basically the same as that in Example 1, except that: the inorganic electron donor filler accounts for 30% of the effective volume of the reactor, and the inorganic electron donor filler is a mixed filler of metallic iron and metallic manganese; the preparation process of the mixed filler of metallic iron and metallic manganese is: after washing metallic manganese twice with a 10% H2SO4 solution by volume, washing it once with deionized water to wash off the oxide coating on the surface; after washing metallic iron twice with a 10% H2SO4 solution by volume, washing it once with deionized water to wash off the oxide coating on the surface; stirring and mixing the washed minerals at room temperature of 25°C under air-tight conditions to evenly mix the metallic manganese powder and the metallic iron powder; the mass ratio of metallic manganese to metallic iron is 1:1.

[0054] According to the steps in Example 1, a double-membrane micro-ecological system of an iron-manganese composite water source denitrification ecological reaction chamber is obtained.

[0055] Example 6: Double membrane micro-ecological system of water source denitrification ecological reaction chamber and its construction method.

[0056] The double membrane micro-ecological system of the water source denitrification ecological reaction cabin provided in Example 6 is basically the same as that in Example 1, except that: the inorganic electron donor filler accounts for 30% of the effective volume of the reactor. The inorganic electron donor filler is a composite filler of metallic iron, metallic manganese and inorganic carbon; the inorganic carbon is activated carbon; the preparation process of the composite filler of metallic iron, metallic manganese and inorganic carbon is: after washing metallic manganese twice with a 10% volume fraction H2SO4 solution, wash it once with deionized water to wash off the oxide coating on the surface; after washing metallic iron twice with a 10% volume fraction H2SO4 solution, wash it once with deionized water to wash off the oxide coating on the surface; the activated carbon is granular, with a particle size of 10 mesh, and a volume density of 0.75g / m 3 , with a specific surface area of ​​285 m2 / g. It was rinsed three times with distilled water before use. The activated carbon was dried and mixed with the washed mineral at 25°C in an air-tight environment to allow the metal powder to adhere to the activated carbon and form a slow-release electron release system.

[0057] According to the steps in Example 1, a composite denitrification and denitrification ecological reaction chamber double membrane micro-ecological system is obtained, which is also called a water source denitrification ecological reaction chamber double membrane micro-ecological system.

[0058] Figure 1 The model diagram of the double membrane micro-ecological system of the ecological reaction chamber of Example 1 of the present invention is shown in FIG. The morphological results of the double membrane micro-ecological system of the denitrification denitrification ecological reaction chamber constructed in Example 1 are as follows: Figure 2 As shown, the morphological results of the double membrane micro-ecological system of the denitrification denitrification ecological reaction chamber constructed in Example 2 are as follows Figure 3As shown. It can be seen that the double-membrane micro-ecological system of the denitrification and denitrification ecological reaction chamber constructed by the present invention has a granular inorganic electron donor filler metal as the core, and the outer layer is wrapped with an ecological reaction chamber double-membrane micro-ecological system composed of a double-layer membrane. Iron-reducing bacteria are detected in the inner layer of the double-membrane micro-ecological system of the ecological reaction chamber, and the iron-reducing bacteria transfer inorganic electrons to the outer layer through microbial action; the outer layer is mainly composed of aerobic denitrifying bacteria, which reduce nitrates in the water body to nitrogen gas through denitrification. Figure 3 It shows that the inorganic electron donor filler metal manganese is oxidized to biological manganese oxide by the action of microbial community, with biological manganese oxide as the core, surrounded or connected by a micro-ecosystem composed of a double-layer membrane. Manganese-reducing bacteria were detected in the inner layer of the micro-ecosystem, which provided inorganic electrons to the outer layer by reducing manganese through microbial action; the outer layer was mainly composed of aerobic denitrifying bacteria, which reduced nitrate in the water to nitrogen gas through denitrification.

[0059] 1. The role of the double-membrane micro-ecological system of the water source denitrification ecological reaction chamber constructed by Examples 1, 2 and 5 of the present invention in removing pollutants in the water environment.

[0060] Overlying water and sediment samples from a reservoir in Yantai, Shandong Province were selected. The overlying water was collected from the surface water at the center of the reservoir. Sediment was collected using a grab-type mud grabber. Water samples and sediments were stored in sterile collection bottles, stored in a portable refrigerator at 4°C and transported back to the laboratory within 48 hours. The water quality parameters were: pH: 7.82 ± 0.30; TN: 17.53 ± 0.26 mg / L; NO3 - -N: 16.76 ± 0.58 mg / L; NO2 - -N:0.15 ± 0.01 mg / L; NH4 + -N: 0.32 ± 0.11 mg / L; TP: 0.22 ± 0.03 mg / L; COD Mn :9.85 ± 0.26 mg / L; Fe: 0.03 ± 0.00 mg / L.

[0061] A 5 L glass reactor was used. Before the experiment, an iron-based denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem, a manganese-based denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem and an iron-manganese composite denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem were constructed according to the method steps in Example 1, Example 2 and Example 5. The reactor groups were set as follows: (1) sediment + overlying water; (2) sediment + overlying water + manganese-based denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem; (3) sediment + overlying water + iron-based denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem; (4) sediment + overlying water + iron-manganese composite denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem.

[0062] The above-mentioned metal manganese and metal iron were purchased from Henan Boyuan Water Purification Materials Co., Ltd. Among them, the amount of sediment added to the reactor was 250 mL, the amount of metal manganese and metal iron added to the reactors of the manganese-based denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem and the iron-based denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem was 5 g / L, the amount of inorganic electron donor filler added to the iron-manganese composite denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem was 5 g / L, and the metal iron filler and metal manganese filler were 2.5 g each.

[0063] All reactors were aerated with oxygen pumps during operation. Water was added to the reactor along the reactor wall using the siphon method. The reactor was operated for two cycles totaling 70 days, with each cycle running for 34 days. Samples were taken every day to measure TN, NO3 — N, NO2 — N, NH4 + -N,COD Mn , TP concentration, set 3 replicates.

[0064] TN, NO3 — N, NO2 — N, NH4 + -N changes with time as Figure 4 and Figure 5 In two reaction cycles, Figure 4 As shown, the control reactor without micro-ecosystem NO3 − -N concentration decreased from 16.46 mg / L to 13.40 and 13.60 mg / L, with removal rates of 18.69% and 17.93%; TN concentration decreased from 17.44 mg / L to 13.54 and 13.88 mg / L, with removal rates of 21.03% and 20.54%, respectively. Figure 5 As shown in (a), the iron-based denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem reactor NO3 − -N concentration decreased from 16.43 mg / L to 0.71 and 0.82 mg / L, with removal rates of 95.67% and 94.57%; TN concentration decreased from 17.09 mg / L to 0.76 and 0.96 mg / L, with removal rates of 95.57% and 94.49%, respectively. Figure 5 As shown in (b), the manganese-based denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem reactor NO3 − -N concentration decreased from 16.36 mg / L to 0.87 and 0.88 mg / L, with removal rates of 94.67% and 94.70%; TN concentration decreased from 17.15 mg / L to 0.97 and 1.01 mg / L, with removal rates of 94.33% and 94.19%, respectively. Figure 5As shown in (c), the iron-manganese composite micro-ecosystem reactor NO3 − -N concentration decreased from 16.57 mg / L to 0.72 and 0.88 mg / L, with removal rates of 95.69% and 94.73%; TN concentration decreased from 17.47 mg / L to 0.71 and 0.93 mg / L, with removal rates of 95.82% and 94.68%, respectively. There was no significant accumulation of nitrite nitrogen and ammonia nitrogen.

[0065] The double membrane micro-ecological system of the denitrification denitrification ecological reaction chamber constructed by the present invention has a great influence on COD Mn The removal ability and removal effect are as follows Figure 6 and Figure 7 In two reaction cycles, Figure 6 As shown, the COD of the control reactor without denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem Mn The concentration decreased from 9.42 mg / L to 4.83-5.11 mg / L, and the removal rates were 48.67% and 45.74%. Figure 7 As shown, the COD of the double membrane micro-ecosystem of the manganese-based denitrification ecological reaction chamber Mn The concentration decreased from 9.40 mg / L to 0.63 and 0.98 mg / L, and the removal rates were 93.21% and 89.58%. Mn The concentration decreased from 9.42 mg / L to 0.73 and 1.11 mg / L, and the removal rates were 92.27% and 88.18%. Mn The concentration decreased from 9.42 mg / L to 0.35 and 1.11 mg / L, with removal efficiencies of 96.31% and 90.77%.

[0066] The removal capacity and effect of the double-membrane micro-ecological system of the denitrification and denitrification ecological reaction chamber constructed by the present invention on TP are as follows: Figure 8 and Fig. 9As shown. In two reaction cycles, the TP concentration of the control reactor without denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem decreased from 0.33 mg / L to 0.14 and 0.16 mg / L, and the removal rate was 56.17% and 52.43%. The TP concentration of the iron-based denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem reactor decreased from 0.33 mg / L to 0.058-0.059 mg / L, and the removal rate was 82.39% and 82.37%. The TP concentration of the manganese-based denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem reactor decreased from 0.33 mg / L to 0.0086 and 0.0090 mg / L, and the removal rate was 93.37% and 97.36%. The TP concentration of the iron-manganese composite micro-ecosystem reactor decreased from 0.33 mg / L to 0.0086-0.02 mg / L, and the removal rate was 93.63% and 93.37%.

[0067] 2. The influence of the double-membrane micro-ecosystem of the denitrification and denitrification ecological reaction chamber constructed by the present invention on the metabolic activity, electron transfer ability and functional enzyme activity of microorganisms in the water environment.

[0068] The iron-based denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem, the manganese-based denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem and the iron-manganese composite denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem were constructed according to the method steps in Example 1, Example 2 and Example 5. The total ATP and electron transfer activity concentration of microorganisms in the water body were measured every day.

[0069] The total ATP concentration of microorganisms in the water of the double membrane micro-ecosystem of different denitrification and denitrification ecological reaction chambers in the early, middle and late stages of the first and second cycles of operation is as follows Fig.10 As shown in (a). At the end of the first cycle, the total ATP concentrations in the control reactor, reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor were 10.94, 60.33, 68.94 and 84.03 nmol / L, respectively. Compared with the control reactor, the total ATP concentrations in the reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor increased by 5.51, 6.30 and 7.69 times, respectively. At the end of the second cycle, the total ATP concentrations in the control reactor, reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor were 10.54, 70.29, 66.83 and 79.20 nmol / L, respectively. Compared with the control reactor, the total ATP concentrations in the reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor increased by 6.67, 6.34 and 7.51 times, respectively.

[0070] The electron transfer activity of microorganisms in the water body in the early, middle and late stages of the first and second cycles of different reactors is as follows: Fig.10 (b) shows. At the end of the first cycle, the concentrations of ETSA in the control reactor, reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor were 0.0012, 0.0039, 0.0035 and 0.0046 μgO2 / g min. Compared with the control reactor, the concentrations of ETSA in the reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor increased by 3.25, 2.92 and 3.83 times. In the second cycle, the concentrations of ETSA in the control reactor, reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor were 0.001, 0.0042, 0.0040 and 0.0051 μg O2 / g min. Compared with the control reactor, the concentrations of ETSA in the reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor increased by 4.20, 4.00 and 5.10 times.

[0071] The relative activities of complex I of the microbial electron transport chain in the water at the early, middle and late stages of each of the two cycles of operation of different reactors are shown in Figure 2. Fig.11 As shown in (a). The relative activities of complex I in the control reactor, reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor in the first cycle were 53.00%, 56.00%, 56.50% and 65.70%. Compared with the control reactor, the relative activities of complex I in the control reactor, reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor increased by 1.06, 1.07 and 1.24 times. The relative activities of complex I in the control reactor, reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor in the second cycle were 53.60%, 55.20%, 57.00% and 56.80%. Compared with the control reactor, the relative activities of complex I in the control reactor, reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor increased by 1.03, 1.07, 1.06 and 1.06 times.

[0072] The relative activities of complex III of the electron transport chain of microorganisms in the water at the early, middle and late stages of each cycle in the two cycles of operation of different reactors are shown in Figure 2. Fig.11As shown in (b). At the end of the first cycle, the relative activities of complex III in the control reactor, reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor were 545.83, 3217.55, 2331.94 and 8489.39 U / mg prot. Compared with the control reactor, the relative activities of complex III in the reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor increased by 5.89, 4.27 and 15.55 times. At the end of the second cycle, the relative activities of complex III in the control reactor, reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor were 633.88, 4956.76, 4022.24 and 10198.66 U / mg prot. Compared with the control reactor, the relative activities of complex III in the reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor increased by 7.82, 5.35 and 16.09 times.

[0073] The relative abundance of microbial denitrification enzymes Nir and Nar in the water at the early, middle and late stages of each cycle in the two cycles of operation of different reactors is shown in Figure 2. Fig.12 As shown. Fig.12 As shown in (a), at the end of the first cycle, the relative abundance of Nir enzymes in the control reactor, reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor were 12.82, 72.69, 68.19 and 92.25 U / mg prot. Compared with the control reactor, the relative abundance of Nir enzymes in the reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor increased by 5.67, 5.55 and 7.20 times. At the end of the second cycle, the relative abundance of Nir enzymes in the control reactor, reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor were 13.09, 89.09, 74.23 and 126.48 U / mg prot. Compared with the control reactor, the relative abundance of Nir enzymes in the reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor increased by 6.81, 5.677 and 9.66 times. Fig.12As shown in (b), the relative abundance of Nar enzyme in the control reactor, reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor at the end of the first cycle was 141.55, 433.64, 423.21 and 455.90 U / mg prot. Compared with the control reactor, the relative abundance of Nar enzyme in the reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor increased by 3.06, 2.99 and 3.22 times. At the end of the second cycle, the relative abundance of Nar enzyme in the control reactor, reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor was 221.72, 410.08, 407.91 and 513.04 U / mg prot. Compared with the control reactor, the relative abundance of Nar enzyme in the reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor increased by 1.85, 1.83 and 2.31 times.

[0074] 3. The bacterial community structure of the double-membrane micro-ecological system of the denitrification and denitrification ecological reaction chamber constructed by the present invention.

[0075] According to the method steps in Example 1, Example 2 and Example 5, an iron-based denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem, a manganese-based denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem and an iron-manganese composite denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem were constructed. Microbial samples were collected from water samples and sediments at the end of the first cycle and the second cycle of the reaction, and stored in a -80°C refrigerator. Metagenomic sequencing was then performed.

[0076] The population structure of microbial communities at the phylum level in the water and sediment of the control group and the manganese / iron enhanced reactor at the end of the first and second cycles of the reaction is as follows Fig.13 As shown. Fig.13As shown in (a), in the water body, Proteobacteria, Actinobacteria, Bacteroidota, Planctomycetota and Firmicutes are the main dominant bacterial phyla. Among them, the abundance of Proteobacteria in the control reactor, reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor at the end of the first cycle was 77.02%, 79.02%, 89.63% and 77.23%, respectively. At the end of the second cycle, the abundance of Proteobacteria in the control reactor, reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor was 92.66%, 67.14%, 64.41% and 72.09%, respectively. The abundance of Actinobacteria in the manganese powder reactor at the end of the first cycle was 4.82%, while the abundance of Actinobacteria in the control reactor was 0.57%. The abundance of Bacteroidota in the control reactor, reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor at the end of the first cycle was 15.24%, 13.87%, 6.71% and 4.95%, respectively. The abundance of Bacteroidota in the control reactor, reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor at the end of the second cycle was 4.14%, 10.83%, 4.47% and 6.12%, respectively. The abundance of Firmicutes in the reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor at the end of the first cycle was less than 1%, while the abundance of Firmicutes in the control reactor was 1.61%. In addition, although Firmicutes did not show dominant growth in the first cycle, its abundance in the reduced manganese reactor, reduced iron reactor and reduced manganese / reduced iron reactor in the second cycle was 16.09%, 22.41% and 7.47%, respectively. Fig.13As shown in (b), in the sediment, Proteobacteria, Actinobacteria, Chloroflexi, Bacteroidota, Acidobacteria, Planctomycetota and Nitrospirae were the main dominant bacterial phyla in the control reactor and the manganese / iron enhanced reactor. The operation of the reactor had little interference with the microorganisms in the sediment. The microbial composition of the sediment samples of each system was similar at the phylum level, and the dominance of the dominant bacterial phyla did not show a significant change. The abundance of Proteobacteria was about 57.19-71.00%, the abundance of Chloroflexi was about 5.78-8.83%, the abundance of Actinobacteria was about 5.99-8.11%, the abundance of Bacteroidota was about 1.89-10.93%, the abundance of Acidobacteria was about 5.78-10.22%, the abundance of Firmicutes was about 0.54-1.17%, the abundance of Planctomycetota was about 2.11-5.41%, and the abundance of Nitrospirae was about 2.79-4.46%.

[0077] Heat maps of the population structure of microbial communities at the family level in the water and sediment of the control group and the manganese / iron enhanced reactor at the end of the first and second cycles of the reaction are shown in Figure 2. Fig.14 As shown. Fig.14 As shown in (a), in the water samples, Comamonadaceae, Burkholderiaceae, Sphingomonadaceae and Methylophilaceae were the dominant bacterial families in the control reactor. In the reactor with added manganese / iron inorganic electron donors, Comamonadaceae, Burkholderiaceae, Sphingomonadaceae, Bacillaceae, Sphaerotilaceae, Caulobacteraceae, Azospirillaceae and Methylophilaceae were the dominant bacterial families. Fig.14As shown in (b), in the sediment samples, Bacillaceae and Moraxellaceae were the dominant families in the control reactor. Comamonadaceae, Methylophilaceae, Sphingomonadaceae, Azospirillaceae, Thiobacillaceae, Nocardiaceae, Rhodobacteraceae, Steroidobacteraceae and Pseudomonadaceae were the dominant families in the reactor with added manganese / iron inorganic electron donors. It should be pointed out that the dominant families Steroidobacteraceae and Comamonadaceae are families with both denitrification and iron and manganese reduction functions, which verifies the feasibility of the method.

[0078] 3. The role of the double-membrane micro-ecological system of the denitrification and denitrification ecological reaction chamber constructed and obtained in Example 2 and Example 4 of the present invention in removing pollutants in the water environment.

[0079] The overlying water and sediment samples of Jinpen Reservoir in Xi'an were selected, and the overlying water was collected from the surface water at the center of the reservoir. Sediments were collected using a grab bucket mud grab. Water samples and sediments were stored in sterile collection bottles, stored in a portable refrigerator at 4℃ and transported back to the laboratory within 48 hours. KNO3 and sodium acetate were added to the water samples to adjust the NO3 − -N and COD concentrations, the carbon-nitrogen ratio of the water body after adjustment is about 1, the initial NO3 − -N concentration is 5 mg / L.

[0080] A 5 L glass reactor was used, and the size of the reactor was 130 mm in inner diameter × 376.7 mm in column height. Before the experiment, a manganese-based denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem and a composite manganese-based denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem were constructed according to the method steps in Example 2 and Example 4. The reactor groups were set as follows: (1) sediment + overlying water; (2) sediment + overlying water + manganese-based denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem; (3) sediment + overlying water + composite manganese-based denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem.

[0081] The above-mentioned manganese metal was purchased from Henan Boyuan Water Purification Materials Co., Ltd. Among them, the amount of sediment added to the reactor was 250 mL, the amount of inorganic electron donor filler added to the double membrane micro-ecosystem of the manganese-based denitrification and denitrification ecological reaction chamber was 5 g / L, the amount of inorganic electron donor filler added to the double membrane micro-ecosystem of the composite manganese-based denitrification and denitrification ecological reaction chamber was 5 g / L, and the manganese metal and activated carbon fillers were 2.5 g each.

[0082] All reactors were aerated with oxygen pumps during operation. Water was added to the reactor along the reactor wall using the siphon method. The reactor was operated for five cycles for a total of 120 days, with each cycle running for 20 days. Samples were taken every 2 days to measure TN and NO3 — N, NO2 — N、NH4 + -N、COD Mn and TP concentration, with 3 replicates.

[0083] TN, NO3 — N, NO2 — N and NH4 + -N changes with time as Fig.15 and Fig.16 In five reaction cycles, Fig.15 As shown, the NO3 − -N concentration decreased from 5.26 mg / L to 5.08 mg / L ~ 4.97 mg / L. − The removal rates of -N were 8.88%, 15.86%, 13.86%, 13.66% and 12.27%. The TN concentration of the control reactor decreased from 5.71 mg / L to 5.18 mg / L ~ 5.04 mg / L. Since the initial concentration of TN was slightly higher than that of NO3 − -N, the removal rates of TN during the operation of the reactor were 22.84%, 20.23%, 20.23%, 20.24% and 14.54%, respectively. Fig.16 As shown in (a), the manganese-based denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem reactor NO3 − -N concentration dropped from 6.36 mg / L to 0.25 mg / L~1.02 mg / L, and the removal rates were 93.13%, 95.85%, 94.32%, 84.53% and 82.57%; TN concentration dropped from 6.48 mg / L to 0.40 mg / L~1.21 mg / L, and the removal rates were 93.88%, 93.56%, 93.57%, 93.56% and 80.13%, respectively. Fig.16 As shown in (b), the composite manganese-based denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem reactor NO3 −-N concentration decreased from 6.14 mg / L to 0.14 mg / L-0.91 mg / L, with removal rates of 94.67% and 94.70%; TN concentration decreased from 17.15 mg / L to 0.97 mg / L and 1.01 mg / L, with removal rates of 94.62%, 97.71%, 97.66%, 97.01% and 84.47%, respectively. Ammonia nitrogen did not accumulate significantly, while nitrite nitrogen concentration showed a slight accumulation in all five cycles, which was then quickly reduced.

[0084] The double membrane micro-ecological system of the denitrification denitrification ecological reaction chamber constructed by the present invention has a great influence on COD Mn The removal ability and removal effect are as follows Fig.17 In five reaction cycles, Fig.17 As shown in (a), the COD of the control reactor without denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem Mn The concentration decreased from 5.39 mg / L to 3.24 mg / L ~ 4.11 mg / L, and the removal rates were 39.85%, 29.22%, 25.48%, 26.73% and 23.82%. Fig.17 As shown in (b), the COD of the double membrane micro-ecosystem of the manganese-based denitrification ecological reaction chamber Mn The concentration dropped from 5.40 mg / L to 0.835 mg / L ~ 1.01 mg / L, and the removal rates were 83.50%, 83.49%, 83.97%, 84.17% and 82.99%. Composite manganese-based denitrification ecological reaction chamber double membrane micro-ecosystem COD Mn The concentration dropped from 5.41 mg / L to 0.60 mg / L ~ 0.84 mg / L, and the removal rates were 71.39%, 88.91%, 86.82%, 88.31% and 86.03%.

[0085] The removal capacity and effect of the double-membrane micro-ecological system of the denitrification and denitrification ecological reaction chamber constructed by the present invention on TP are as follows: Fig.18As shown. In five reaction cycles, the TP concentration of the control reactor without denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem decreased from 0.34 mg / L to 0.19 mg / L ~ 0.27 mg / L, and the removal rates were 36.43%, 32.49%, 43.32%, 25.27% and 21.66%. The TP concentration of the manganese-based denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem reactor decreased from 0.34 mg / L to 0.03 mg / L ~ 0.12 mg / L, and the removal rates were 89.07%, 90.25%, 86.64%, 68.59% and 64.98%. The TP concentration of the composite manganese-based denitrification and denitrification ecological reaction chamber double membrane micro-ecosystem reactor decreased from 0.34 mg / L to 0.03 mg / L ~ 0.09 mg / L, and the removal rates were 89.08%, 90.25%, 86.64%, 75.82% and 72.20%.

[0086] Although preferred embodiments of the present invention have been described, additional changes and modifications may occur to these embodiments once those skilled in the art are aware of the basic inventive concepts.

[0087] Obviously, those skilled in the art may make various changes and modifications to the present invention without departing from the spirit and scope of the present invention. Thus, if these modifications and variations of the present invention fall within the scope of the claims of the present invention and their equivalents, the present invention is also intended to include these modifications and variations.

Claims

1. A method for constructing a double-membrane micro-ecological system for a water source denitrification ecological reaction chamber, characterized in that: The steps include: Inorganic electron donor fillers with a volume fraction of 10% to 40% are added to the reactor, and an aerobic / anaerobic alternating environment is created through intermittent aeration. During the intermittent aeration process, the ratio of aeration time to interval time is 10 h to 12 h:12 h. Reservoir source water is introduced by intermittent water inflow. During the intermittent water inflow process, the hydraulic retention time in the reactor is 3 d to 7 d, and the water inflow time is 1 h to 2 h. The intermittent water inflow step is repeated 3 to 5 times. Aerobic denitrification enhanced denitrification part is generated on the surface of the inorganic electron donor filler, and a double-membrane micro-ecological system of the denitrification denitrification ecological reaction cabin is obtained.

2. The method for constructing a double-membrane micro-ecological system for a water source denitrification ecological reaction chamber according to claim 1, characterized in that: The filler containing an inorganic electron donor is a mineral filler or a composite filler of a mineral filler and an inorganic carbon.

3. The method for constructing a double-membrane micro-ecological system for a water source denitrification ecological reaction chamber according to claim 2, characterized in that: The mineral filler is a metallic iron filler, a metallic manganese filler or a composite filler of metallic iron and metallic manganese.

4. The method for constructing a double-membrane micro-ecological system for a water source denitrification ecological reaction chamber according to claim 2, characterized in that: The inorganic carbon is activated carbon or biochar.

5. The method for constructing a double-membrane micro-ecological system for a water source denitrification ecological reaction chamber according to claim 2, characterized in that: The mineral filler and inorganic carbon composite filler is made of mineral filler and inorganic carbon in a mass ratio of 1-5:1-5.

6. The method for constructing a double-membrane micro-ecological system for a water source denitrification ecological reaction chamber according to claim 2, characterized in that: The preparation process of the mineral filler and inorganic carbon composite filler is as follows: washing the inorganic carbon and the mineral filler with distilled water and a H2SO4 solution with a volume fraction of 10% to 20% in sequence, drying, stirring and mixing, and obtaining the mineral filler and inorganic carbon composite filler.

7. The method for constructing a double-membrane micro-ecological system for a water source denitrification ecological reaction chamber according to claim 1, characterized in that: The aeration rate of the intermittent aeration is 10L gas / min / cubic meter to 15L gas / min / cubic meter.

8. A water source denitrification ecological reaction chamber double membrane micro-ecological system, wherein the water source denitrification ecological reaction chamber double membrane micro-ecological system is constructed based on the construction method according to any one of claims 1 to 7, characterized in that: It includes inorganic electron donors and the aerobic denitrification enhanced denitrification part formed on their surface.

9. An application of a water source denitrification ecological reaction chamber double membrane micro-ecological system in water treatment, the application is based on the water source denitrification ecological reaction chamber double membrane micro-ecological system according to claim 8, characterized in that: The double-membrane micro-ecological system of the denitrification denitrification ecological reaction chamber is used for denitrification of water bodies in water source reservoirs.

10. The use of the double membrane micro-ecological system of the water source denitrification ecological reaction chamber according to claim 9 in water treatment is characterized in that: The denitrification is to reduce the content of total nitrogen, nitrate, nitrite and ammonia in the water environment.

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