Water source denitrification ecological reaction cabin double-membrane micro-ecosystem, construction method and application thereof

Abstract

The present application relates to the field of environmental water treatment technology, and discloses a water source denitrification ecological reaction cabin double-membrane micro-ecosystem, a construction method and application thereof. The method comprises the following steps: adding inorganic electron donor filler into a reactor; achieving an aerobic / anaerobic environment alternation through intermittent aeration; using intermittent water feeding to pass the reservoir source water into the reactor filled with inorganic electron donor filler; repeating the intermittent water feeding step for 3-5 times until an aerobic denitrification enhanced denitrification part is formed on the surface of the inorganic electron donor. The denitrification ecological reaction cabin double-membrane micro-ecosystem constructed by the present application effectively reduces the concentration of nitrogen pollutants and COD pollutants in the micro-polluted water body, solves the problem of efficiency reduction caused by the lack of electron donor in the water body, and meets the practical requirements of micro-polluted water body treatment.

Description

TECHNICAL FIELD

[0001] The present application relates to the technical field of environmental water treatment, in particular to a water source denitrification ecological reaction cabin double-membrane micro-ecosystem and a construction method and application thereof. BACKGROUND

[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 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, most of the polluted water bodies are in a state of slight pollution, and the pollutant concentration is relatively low, but the influence on the water ecosystem cannot be ignored. In the field of environmental water treatment, especially for the purification of water in water source reservoirs, traditional treatment methods often have certain limitations, such as physical sedimentation, chemical flocculation, etc. Although these methods can remove some pollutants to some extent, they often have problems such as low treatment efficiency, high cost, and secondary pollution. In terms of biological treatment, due to the lack of electron donors in slightly polluted water bodies, traditional biological treatment methods often fail to achieve ideal treatment results, resulting in a decrease in treatment efficiency.

[0003] At present, there are few researches on the technology of strengthening the activity of indigenous aerobic denitrifying bacteria in slightly polluted water bodies to achieve efficient denitrification. When treating low-carbon-nitrogen ratio water source water, the additional organic carbon source may cause the risk of secondary pollution and increase the treatment cost. At present, the treatment of slightly polluted water bodies is mainly through oxygenation of the water body, but oxygenation can only inhibit the anaerobic release of nutrients in the water body sediment, and cannot fundamentally improve the water quality. Therefore, it is urgent to develop an environmentally friendly method for improving the water quality of lake-type water source. SUMMARY

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

[0005] The present application provides a construction method of a denitrification ecological reaction cabin double-membrane micro-ecosystem, comprising the following steps:

[0006] The inorganic electron donor filler is added in the reactor in a volume fraction of 10% to 40%, and an aerobic / anaerobic alternating environment is created by intermittent aeration, the ratio of aeration time to interval time is 10h to 12h:12h, the reservoir source water is introduced by intermittent water feeding, the hydraulic retention time in the reactor is 3d to 7d, the water feeding time is 1h to 2h, the intermittent water feeding step is repeated 3 to 5 times, until the aerobic denitrification enhanced nitrogen removal part is generated on the surface of the inorganic electron donor filler, and the denitrification ecological reaction cabin double-membrane micro-ecosystem is obtained.

[0007] The denitrification ecological reaction cabin double-membrane micro-ecosystem is obtained by the construction method of the denitrification ecological reaction cabin double-membrane micro-ecosystem, the aerobic denitrification enhanced nitrogen removal part is generated on the surface of the inorganic electron donor filler, and the denitrification ecological reaction cabin double-membrane micro-ecosystem is obtained. The aerobic denitrification microorganism membrane in the aerobic denitrification enhanced nitrogen removal part is coupled with the inorganic electron donor to enhance the nitrogen removal. The content of total nitrogen, nitrate, nitrite and ammonia in the water environment is effectively reduced.

[0008] The application also provides the denitrification ecological reaction cabin double-membrane micro-ecosystem obtained by the construction method, which comprises the inorganic electron donor and the aerobic denitrification enhanced nitrogen removal part formed on the surface of the inorganic electron donor.

[0009] The application also provides the application of the denitrification ecological reaction cabin double-membrane micro-ecosystem in water treatment, and the denitrification ecological reaction cabin double-membrane micro-ecosystem is used for denitrification of water in a water source reservoir.

[0010] Compared with the prior art, the application has the following beneficial effects:

[0011] The construction method provided by the application combines the inorganic electron donor with indigenous bacteria colonies, creates an aerobic / anaerobic alternating environment by intermittent aeration, and pumps the water body to circulate at a low speed to fully contact and react with the filler, so that the ecological reaction cabin double-membrane micro-ecosystem is formed on the surface of the inorganic electron donor filler. The water source denitrification ecological reaction cabin double-membrane micro-ecosystem comprises the inorganic electron donor and the aerobic denitrification enhanced nitrogen removal part formed on the surface of the inorganic electron donor. The water source denitrification ecological reaction cabin double-membrane micro-ecosystem 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, the inorganic electron donor is reduced by metal-reducing bacteria, and the electrons are transmitted to the outer layer; the outer layer is the aerobic denitrification enhanced nitrogen removal part, and indigenous aerobic denitrifying bacteria receive the electrons provided by the inner layer to perform denitrification, so that the nitrate in the water body is oxidized into nitrogen gas to remove nitrogen, the defects of lack of sufficient electron donors in the slightly polluted water body are solved, the removal efficiency of nitrogen and COD pollutants in the water body can be effectively improved, and the practical requirements of the slightly polluted water body treatment are met.

[0012] The inorganic electron donor filler of the present application is made of a certain mass of metal or its compound, the metal provides electrons for the reaction system, solves the defects of insufficient organic carbon electron donor of source water, and improves the denitrification ability 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.

[0013] The present application is suitable for the treatment of various micro-polluted water bodies by constructing a specific micro-ecosystem, promotes the diversity and ecological balance of microorganisms in the water body, reduces the use of chemical reagents, reduces the secondary pollution to the environment, and promotes the long-term health of the water body. The micro-ecosystem is simple to operate, easy to realize automatic control, suitable for large-scale application, meets the practical requirements of micro-polluted water body treatment, has strong adaptability and wide application prospect. BRIEF DESCRIPTION OF DRAWINGS

[0014] In order to more clearly illustrate the technical solutions in the embodiments of the present application or the prior art, the drawings needed to be used in the embodiments or prior art description will be briefly introduced below. Obviously, the drawings in the following description are only some embodiments of the present application, and other drawings can be obtained by those skilled in the art without creative labor.

[0015] Figure 1 It is a double-membrane micro-ecosystem model diagram of the water source denitrification ecological reaction cabin of embodiment 1 of the present application.

[0016] Figure 2 It is a scanning electron microscope diagram of the double-membrane micro-ecosystem of the water source denitrification ecological reaction cabin constructed by taking iron as inorganic electron donor filler of embodiment 2 of the present application.

[0017] Figure 3 It is a scanning electron microscope diagram of the double-membrane micro-ecosystem of the water source denitrification ecological reaction cabin constructed by taking manganese as inorganic electron donor filler of embodiment 2 of the present application.

[0018] Figure 4 It is a diagram of the determination results of the nitrogen concentration change and nitrogen removal rate of the water body in two reaction periods of the double-membrane micro-ecosystem reactor of the present application.

[0019] Figure 5 It is a diagram of the determination results of the nitrogen concentration change and nitrogen removal rate of the water body in two reaction periods of the double-membrane micro-ecosystem reactor of the present application.

[0020] In the figure, (a) is the removal of nitrogen by the iron-based double-membrane micro-ecosystem of the water source denitrification ecological reaction cabin, the left side of the figure shows the change of nitrogen concentration at different times, and the right side of the figure shows the change of nitrogen removal efficiency at different times.

[0021] (b) nitrogen removal by the double-membrane micro-ecological system of the manganese-based water source denitrification ecological reactor;

[0022] (c) nitrogen removal by the double-membrane micro-ecological system of the iron-manganese composite water source denitrification ecological reactor.

[0023] Figure 6 Fig. 2 is a diagram of the determination results of the concentration change and removal rate of the water body COD in the double-membrane micro-ecological system reactor without water source denitrification ecological reactor in Example 3 of the present application in two reaction periods. Mn Fig. 3 is a diagram of the determination results of the concentration change and removal rate of the water body COD in the double-membrane micro-ecological system reactor with water source denitrification ecological reactor in Example 3 of the present application in two reaction periods.

[0024] Figure 7 Fig. 4 is a diagram of the determination results of the concentration change and removal rate of the water body TP in the double-membrane micro-ecological system reactor without water source denitrification ecological reactor in Example 3 of the present application in two reaction periods. Mn Fig. 5 is a diagram of the determination results of the concentration change and removal rate of the water body TP in the double-membrane micro-ecological system reactor with water source denitrification ecological reactor in Example 3 of the present application in two reaction periods.

[0025] Figure 8 Fig. 6 is a diagram of the determination results of the concentration change and removal rate of the water body TP in the double-membrane micro-ecological system reactor without water source denitrification ecological reactor in Example 3 of the present application in two reaction periods.

[0026] Figure 9 Fig. 7 is a diagram of the determination results of the concentration change and removal rate of the water body TP in the double-membrane micro-ecological system reactor with water source denitrification ecological reactor in Example 3 of the present application in two reaction periods.

[0027] Figure 10 Fig. 8 is a columnar diagram of the determination results of the concentration change of the total microbial ATP and ETSA in the double-membrane micro-ecological system reactor with water source denitrification ecological reactor in Example 4 of the present application in two reaction periods.

[0028] Fig. 8(a) is a diagram of the concentration change of the total microbial ATP in the reactor in two reaction periods;

[0029] Fig. 8(b) is a diagram of the concentration change of the total microbial ETSA in the reactor in two reaction periods.

[0030] Figure 11 Fig. 9 is a columnar diagram of the determination results of the relative activity change of complex I and complex III in the water body in the double-membrane micro-ecological system reactor with water source denitrification ecological reactor in Example 4 of the present application in two reaction periods.

[0031] Fig. 9(a) is a diagram of the relative activity change of complex I in the water body in the reactor in two reaction periods;

[0032] Fig. 9(b) is a diagram of the relative activity change of complex III in the water body in the reactor in two reaction periods.

[0033] Figure 12This is a bar chart showing the results of measuring the abundance of Nar and Nir enzymes in the water body during two reaction cycles in the dual-membrane micro-ecosystem reactor of the water source denitrification ecological reaction chamber in Example 4 of the present invention.

[0034] In the figure, (a) represents the abundance of Nir enzyme in the water during two reaction cycles of the reactor;

[0035] (b) represents the abundance of Nar enzyme in the water during the two reaction cycles of the reactor.

[0036] Figure 13 This is a bar chart showing the percentage of phylum-level bacterial communities in the water body during two reaction cycles in the dual-membrane micro-ecosystem reactor of the water source denitrification ecological reaction chamber in Embodiment 5 of the present invention.

[0037] In the figure, (a) shows the phylum-level bacterial community in the water body during two reaction cycles of the reactor;

[0038] (b) phylum-level bacterial community in the sediment during two reaction cycles of the reactor.

[0039] Figure 14 This is a heat map of the bacterial community at different levels in the water body during two reaction cycles in the dual-membrane micro-ecosystem reactor of the water source denitrification ecological reaction chamber in Application Example 5 of the present invention.

[0040] In the figure, (a) shows the bacterial community at different levels in the water body during two reaction cycles of the reactor;

[0041] (b) shows the level of bacterial community in the sediment during two reaction cycles of the reactor.

[0042] Figure 15 The figure shows the results of measuring the changes in water nitrogen concentration and nitrogen removal rate in the dual-membrane micro-ecosystem reactor without denitrification in this invention over five reaction cycles.

[0043] Figure 16 The figure shows the results of measuring the changes in nitrogen concentration and nitrogen removal rate in the water body during five reaction cycles of the dual-membrane micro-ecosystem of the denitrification and nitrogen removal ecological reaction chamber constructed in this invention.

[0044] In the figure, (a) shows the nitrogen removal by the dual-membrane micro-ecosystem of the manganese-based denitrification denitrification ecological reaction chamber;

[0045] (b) Nitrogen removal by the dual-membrane micro-ecosystem of the composite manganese-based denitrification denitrification ecological reaction chamber;

[0046] Figure 17 The present invention relates to the COD of water bodies in a dual-membrane micro-ecosystem reactor with and without a denitrification ecological reaction chamber, and a dual-membrane micro-ecosystem reactor with a denitrification ecological reaction chamber, over five reaction cycles. Mn Graph showing concentration changes and removal rate measurements;

[0047] In the figure, (a) shows the effect of the dual-membrane micro-ecosystem of the denitrification-free denitrification ecological reaction chamber on COD. Mn The removal status;

[0048] (b) The effects of the manganese-based denitrification ecological reaction chamber dual-membrane micro-ecosystem and the composite manganese-based denitrification ecological reaction chamber dual-membrane micro-ecosystem on COD Mn The removal status.

[0049] Figure 18 The figure shows the changes in TP concentration and removal rate in the water body during five reaction cycles in the dual-membrane micro-ecosystem reactor with and without denitrification ecological reaction chamber of the present invention.

[0050] In the figure, (a) shows the removal of TP by the dual-membrane micro-ecosystem of the denitrification-free denitrification ecological reaction chamber;

[0051] (b) shows the removal of TP by the manganese-based denitrification denitrification ecological reaction chamber dual-membrane micro-ecosystem and the composite manganese-based denitrification denitrification ecological reaction chamber dual-membrane micro-ecosystem. Detailed Implementation

[0052] The specific embodiments of the present invention are described in detail below, but it should be understood that the scope of protection of the present invention is not limited to the specific embodiments. Based on the embodiments of the present invention, all other embodiments obtained by those skilled in the art without creative effort are within the scope of protection of the present invention. Unless otherwise specified, the experimental methods described in the embodiments of the present invention are conventional methods, and the materials and reagents used in the following embodiments are commercially available unless otherwise specified.

[0053] Example 1: A dual-membrane micro-ecosystem for water source denitrification and its construction method.

[0054] The reactor is filled with inorganic electron donor packing material, which is packing material containing inorganic electron donors. The inorganic electron donor packing material accounts for 40% of the volume fraction of the reactor, with a certain amount of reserved space.

[0055] The reactor is a cylindrical reactor made of transparent acrylic glass with a volume of 5 L and dimensions of 130 mm inner diameter × 376.7 mm column height. The inorganic electron donor packing is metallic iron packing, specifically iron powder.

[0056] After being filled with inorganic electron donor packing material, the reactor is intermittently aerated using an oxygenation pump. The aeration time-interval ratio is set at 12 h:12 h, and the aeration rate is 15 L gas / min / m³, creating an alternating aerobic / anaerobic environment to promote the growth of different types of bacteria. Reservoir source water is intermittently introduced, and a pump drives the water flow at a low speed to circulate the source water until the reactor is full. The water flow encounters resistance at the packing material, resulting in uneven velocity distribution and circulation, which promotes contact between the packing material and the water, increasing the impact on the water. The hydraulic retention time in the reactor during intermittent water introduction is 5 days, with each water introduction lasting 2 hours. This process is repeated 5 times, generating an aerobic denitrification-enhanced denitrification component on the surface of the inorganic electron donor packing material, thus obtaining a dual-membrane micro-ecosystem for iron-based water source denitrification in the ecological reaction chamber.

[0057] The ecological reaction chamber consists of a dual-membrane micro-ecosystem, comprising: an inner layer: an anaerobic / facultative anaerobic autotrophic microbial inorganic electron donor reduction section, in which inorganic electron donors are reduced by metal-reducing bacteria, providing electrons to the outer layer; and an outer layer: an aerobic denitrification enhanced nitrogen removal section, in which indigenous aerobic denitrifying bacteria absorb electrons provided by the inner layer for oxidation, thereby removing pollutants and nitrogen from the water.

[0058] Inorganic electron donors continuously provide electron donors to 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 dual-membrane micro-ecosystem is used for denitrification and removal of pollutants such as COD in water source reservoirs.

[0059] The source water is from a severely eutrophic lake reservoir, originating from a reservoir in Yantai City, Shandong Province. The source water temperature is maintained above 10℃. The reservoir water provides the nutrients required for its survival. The aeration equipment's oxygen pump provides dissolved oxygen, operating intermittently in 12-hour cycles to release air into the reactor water, forming a gas-water mixture with microbubbles in full contact with the water, achieving an overall alternating aerobic and anaerobic environment. Simultaneously, the pump drives the water flow at a low speed to provide the necessary conditions for the construction of the dual-membrane micro-ecosystem of the water source denitrification ecological reaction chamber. The metal packing provides an external electron donor for the system. During the construction process, the metal packing is in full contact with the water, allowing the system to maintain its activity, generation renewal, and denitrification capacity.

[0060] Table 1. Water quality parameters of a water source reservoir in Yantai

[0061]

[0062] Example 2: A dual-membrane micro-ecosystem for water source denitrification ecological reaction chamber and its construction method.

[0063] The dual-membrane micro-ecosystem of the water source denitrification ecological reaction chamber provided in Example 2 is basically the same as that in Example 1, except that the inorganic electron donor packing accounts for 30% of the effective volume of the reactor. The inorganic electron donor packing is a manganese metal packing, which is manganese powder. The manganese-based water source denitrification ecological reaction chamber dual-membrane micro-ecosystem is obtained by following the steps in Example 1.

[0064] Example 3: A dual-membrane micro-ecosystem for water source denitrification and its construction method.

[0065] The dual-membrane micro-ecosystem 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 packing is a composite packing of metallic iron and inorganic carbon; and the inorganic carbon is activated carbon. The preparation process of the composite packing of metallic iron and inorganic carbon is as follows: the metallic iron is washed twice with a 10% (v / v) H2SO4 solution, and then washed once with deionized water to remove the oxide coating on the surface; the activated carbon is granular with a particle size of 16 mesh and a bulk density of 0.75 g / m³. 3 The specific surface area is 285 m² / g. Before use, the activated carbon is rinsed three times with distilled water. After drying, the activated carbon is mixed with washed metallic iron at 25°C in the absence of air, allowing the iron powder to adhere to the activated carbon and form a slow-release electron release system. The mass ratio of metallic iron to activated carbon is 1:1.

[0066] The composite iron-based water denitrification ecological reaction chamber dual-membrane micro-ecosystem was obtained by following the steps in Example 1.

[0067] Example 4: A dual-membrane micro-ecosystem for water source denitrification and its construction method.

[0068] The dual-membrane micro-ecosystem 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 packing accounts for 30% of the effective volume of the reactor, and the inorganic electron donor packing is a composite packing of metallic manganese and inorganic carbon; the inorganic carbon is activated carbon. The preparation process of the metallic manganese and inorganic carbon composite packing is as follows: the metallic manganese is washed twice with a 10% (v / v) H2SO4 solution, and then washed once with deionized water to remove the oxide coating on the surface; the activated carbon is granular with a particle size of 16 mesh and a bulk density of 0.75 g / m³. 3 The specific surface area is 285 m² / g. Before use, the activated carbon is rinsed three times with distilled water. After drying, the activated carbon is mixed with the washed minerals at 25°C in the absence of air, allowing the manganese powder to adhere to the activated carbon and form a slow-release electron release system. The mass ratio of manganese to activated carbon is 1:1.

[0069] The composite manganese-based water source denitrification ecological reaction chamber dual-membrane micro-ecosystem was obtained by following the steps in Example 1.

[0070] Example 5: A dual-membrane micro-ecosystem for water source denitrification and its construction method.

[0071] The dual-membrane micro-ecosystem of the water source denitrification ecological reaction chamber provided in Example 5 is basically the same as that in Example 1, except that: the inorganic electron donor packing accounts for 30% of the effective volume of the reactor, and the inorganic electron donor packing is a mixed packing of metallic iron and metallic manganese; the preparation process of the mixed packing of metallic iron and metallic manganese is as follows: metallic manganese is washed twice with a 10% H2SO4 solution, and then washed once with deionized water to remove the oxide coating on the surface; metallic iron is washed twice with a 10% H2SO4 solution, and then washed once with deionized water to remove the oxide coating on the surface; the washed minerals are stirred and mixed at 25°C in the absence of air to make the metallic manganese powder and metallic iron powder evenly mixed; the mass ratio of metallic manganese to metallic iron is 1:1.

[0072] The iron-manganese composite water source denitrification ecological reaction chamber dual-membrane micro-ecosystem was obtained by following the steps in Example 1.

[0073] Example 6: Water source denitrification ecological reaction chamber dual-membrane micro-ecosystem and its construction method.

[0074] The dual-membrane micro-ecosystem of the water source denitrification ecological reaction chamber provided in Example 6 is basically the same as that in Example 1, except that: the inorganic electron donor packing accounts for 30% of the effective volume of the reactor. The inorganic electron donor packing is a composite packing of metallic iron, metallic manganese, and inorganic carbon; the inorganic carbon is activated carbon; the preparation process of the composite packing of metallic iron, metallic manganese, and inorganic carbon is as follows: metallic manganese is washed twice with a 10% H2SO4 solution, and then washed once with deionized water to remove the oxide coating on the surface; metallic iron is washed twice with a 10% H2SO4 solution, and then washed once with deionized water to remove the oxide coating on the surface; the activated carbon is granular with a particle size of 10 mesh and a bulk density of 0.75 g / m³. 3 The specific surface area is 285 m² / g. It is rinsed three times with distilled water before use. After drying, the activated carbon is mixed with the washed minerals at 25°C in the absence of air, so that the metal powder adheres to the activated carbon to form a slow-release electron release system.

[0075] The composite denitrification denitrification ecological reaction chamber dual-membrane micro-ecosystem, also known as the water source denitrification ecological reaction chamber dual-membrane micro-ecosystem, was obtained by following the steps in Example 1.

[0076] Figure 1This is a model diagram of the dual-membrane micro-ecosystem of the ecological reaction chamber in Example 1 of the present invention. The morphological results of the dual-membrane micro-ecosystem of the denitrification ecological reaction chamber obtained in Example 1 are as follows: Figure 2 As shown, the morphological results of the dual-membrane micro-ecosystem of the denitrification and nitrogen removal ecological reaction chamber obtained in Example 2 are as follows: Figure 3 As shown, the denitrification and nitrogen removal ecological reaction chamber dual-membrane micro-ecosystem constructed in this invention uses granular inorganic electron donor packing metal as its core, and is wrapped by an outer layer composed of a double-membrane ecological reaction chamber. Iron-reducing bacteria were detected in the inner layer of this ecological reaction chamber dual-membrane micro-ecosystem, which transfers 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 to nitrogen gas through denitrification. Figure 3 This indicates that, through the action of microbial communities, the inorganic electron donor material, metallic manganese, is oxidized into biogenic manganese oxide. This biogenic manganese oxide forms the core, surrounded or connected by a micro-ecosystem composed of a double-layered membrane. Manganese-reducing bacteria were detected in the inner layer of this micro-ecosystem. These bacteria, through microbial action, reduce manganese and provide inorganic electrons to the outer layer. The outer layer is mainly composed of aerobic denitrifying bacteria, which reduce nitrates in the water to nitrogen gas through denitrification.

[0077] I. The role of the dual-membrane micro-ecosystem of water source denitrification ecological reaction chamber obtained by the present invention in the removal of pollutants in the aquatic environment.

[0078] Water and sediment samples were collected from the surface water of a reservoir in Yantai, Shandong Province. The surface water was collected at the center of the reservoir. Sediment samples were collected using a grab bucket sludge collector. Both water and sediment samples were stored in sterile collection bottles 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.

[0079] A 5 L glass reactor was used. Before the experiment, the iron-based denitrification denitrification ecological reaction chamber dual-membrane micro-ecosystem, the manganese-based denitrification denitrification ecological reaction chamber dual-membrane micro-ecosystem, and the iron-manganese composite denitrification denitrification ecological reaction chamber dual-membrane micro-ecosystem were constructed according to the methods and steps in Examples 1, 2, and 5. The reactor groups were set as follows: (1) sediment + overlying water; (2) sediment + overlying water + manganese-based denitrification denitrification ecological reaction chamber dual-membrane micro-ecosystem; (3) sediment + overlying water + iron-based denitrification denitrification ecological reaction chamber dual-membrane micro-ecosystem; (4) sediment + overlying water + iron-manganese composite denitrification denitrification ecological reaction chamber dual-membrane micro-ecosystem.

[0080] The aforementioned manganese and iron were purchased from Henan Boyuan Water Purification Materials Co., Ltd. Specifically, the amount of sediment added to the reactor was 250 mL; the amount of manganese and iron added to the manganese-based and iron-based denitrification ecological reactor dual-membrane micro-ecosystems was 5 g / L; the amount of inorganic electron donor packing in the iron-manganese composite denitrification ecological reactor dual-membrane micro-ecosystem was 5 g / L; and 2.5 g each of iron and manganese packing were used.

[0081] All reactors were aerated using oxygen pumps during operation. Source water was added to the reactors via siphon along the reactor wall. The reactors operated for two cycles totaling 70 days, with each cycle lasting 34 days. Total nitrogen (TN) and nitrogen oxides (NO3) were measured daily. — N, NO2 — N, NH4 + -N, COD Mn TP concentration, set up 3 replicates.

[0082] TN, NO3 — N, NO2 — N, NH4 + -N changes over time as follows Figure 4 and Figure 5 As shown. Within two reaction cycles, as... Figure 4 As shown, the control reactor NO3 without a micro-ecosystem − -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%, respectively; 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 denitrification ecological reaction chamber dual-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%, respectively; 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 denitrification ecological reaction chamber dual-membrane micro-ecosystem reactor NO3 − -N concentrations decreased from 16.36 mg / L to 0.87 and 0.88 mg / L, with removal rates of 94.67% and 94.70%, respectively; TN concentrations 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 5 As shown in (c), the iron-manganese composite micro-ecosystem reactor NO3 − Nitrogen (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%, respectively; nitrogen (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. No significant accumulation of nitrite or ammonia nitrogen was observed.

[0083] The dual-membrane micro-ecosystem of the denitrification and nitrogen removal ecological reaction chamber constructed in this invention has a positive effect on COD. Mn Its removal ability and removal effect are as follows Figure 6 and Figure 7 As shown. Within two reaction cycles, as... Figure 6 As shown, the control reactor of the dual-membrane micro-ecosystem without denitrification denitrification ecological reaction chamber has a COD... Mn The concentration decreased from 9.42 mg / L to 4.83-5.11 mg / L, with removal rates of 48.67% and 45.74%, respectively. Figure 7 As shown, the manganese-based denitrification denitrification ecological reaction chamber dual-membrane micro-ecosystem COD Mn The concentrations decreased from 9.40 mg / L to 0.63 and 0.98 mg / L, respectively, with removal rates of 93.21% and 89.58%. The iron-based denitrification denitrification ecological reaction chamber with dual-membrane micro-ecosystem COD... Mn The concentration decreased from 9.42 mg / L to 0.73 and 1.11 mg / L, respectively, with removal rates of 92.27% and 88.18%. The iron-manganese composite denitrification denitrification ecological reaction chamber with dual-membrane micro-ecosystem COD... Mn The concentrations decreased from 9.42 mg / L to 0.35 and 1.11 mg / L, with removal rates of 96.31% and 90.77%, respectively.

[0084] The denitrification and nitrogen removal ecological reaction chamber dual-membrane micro-ecosystem constructed in this invention exhibits the following removal capacity and effect on TP: Figure 8and Figure 9 As shown in the figure, within two reaction cycles, the TP concentration in the control reactor of the denitrification-free denitrification ecological reactor with dual membrane micro-ecosystem decreased from 0.33 mg / L to 0.14 and 0.16 mg / L, with removal rates of 56.17% and 52.43%, respectively. In the iron-based denitrification denitrification ecological reactor with dual membrane micro-ecosystem, the TP concentration decreased from 0.33 mg / L to 0.058-0.059 mg / L, with removal rates of 82.39% and 82.37%, respectively. In the manganese-based denitrification denitrification ecological reactor with dual membrane micro-ecosystem, the TP concentration decreased from 0.33 mg / L to 0.0086 and 0.0090 mg / L, with removal rates of 93.37% and 97.36%, respectively. In the iron-manganese composite micro-ecosystem reactor, the TP concentration decreased from 0.33 mg / L to 0.0086-0.02 mg / L, with removal rates of 93.63% and 93.37%, respectively.

[0085] II. The effects of the denitrification and nitrogen removal ecological reaction chamber dual-membrane micro-ecosystem constructed in this invention on the metabolic activity, electron transfer capacity and functional enzyme activity of microorganisms in the aquatic environment.

[0086] Following the methods and steps described in Examples 1, 2, and 5, a dual-membrane micro-ecosystem for iron-based denitrification and nitrogen removal in an ecological reaction chamber, a dual-membrane micro-ecosystem for manganese-based denitrification and nitrogen removal in an ecological reaction chamber, and a dual-membrane micro-ecosystem for iron-manganese composite denitrification and nitrogen removal in an ecological reaction chamber were constructed and obtained. The concentrations of total ATP and electron transport activity of the microorganisms in the water were measured daily.

[0087] The total ATP concentration of microorganisms in the water body during the early, middle, and late stages of the first and second cycles of operation of different denitrification and nitrogen removal ecological reaction chambers with dual membrane micro-ecosystems is as follows: Figure 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 to 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 to 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.

[0088] Electron transport activity of microorganisms in the water during the early, middle, and late stages of the first and second cycles of operation in different reactors, as follows: Figure 10 As shown in (b). The concentrations of ETSA in the control reactor, reduced manganese reactor, reduced iron reactor, and reduced manganese / reduced iron reactor during the final stage of the first cycle were 0.0012, 0.0039, 0.0035, and 0.0046 μg O2 / g min, respectively. Compared to 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, respectively. The concentrations of ETSA in the control reactor, reduced manganese reactor, reduced iron reactor, and reduced manganese / reduced iron reactor during the second cycle were 0.001, 0.0042, 0.0040, and 0.0051 μg O2 / g min, respectively. Compared to 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, respectively.

[0089] The relative activity of microbial electron transport chain complex I in the water body during the early, middle, and late stages of each of the two operating cycles of different reactors is as follows: Figure 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 during the first cycle of operation were 53.00%, 56.00%, 56.50%, and 65.70%, respectively. Compared to 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, respectively. The relative activities of Complex I in the control reactor, reduced manganese reactor, reduced iron reactor, and reduced manganese / reduced iron reactor during the second cycle of operation were 53.60%, 55.20%, 57.00%, and 56.80%, respectively. Compared to 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, respectively.

[0090] The relative activity of microbial electron transport chain complex III in the water body during the early, middle, and late stages of each of the two operating cycles of different reactors is as follows: Figure 11As shown in (b). The relative activities of Complex III in the control reactor, reduced manganese reactor, reduced iron reactor, and reduced manganese / reduced iron reactor at the end of the first cycle were 545.83, 3217.55, 2331.94, and 8489.39 U / mg prot, respectively. Compared to 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, respectively. The relative activities of Complex III in the control reactor, reduced manganese reactor, reduced iron reactor, and reduced manganese / reduced iron reactor at the end of the second cycle were 633.88, 4956.76, 4022.24, and 10198.66 U / mg prot, respectively. Compared to 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, respectively.

[0091] The relative abundances of microbial denitrification functional enzymes Nir and Nar in the water during the early, middle, and late stages of each of the two operating cycles of different reactors are as follows: Figure 12 As shown. Figure 12 As shown in (a), the relative abundance of Nir enzyme in the control reactor, reduced manganese reactor, reduced iron reactor, and reduced manganese / reduced iron reactor during the first cycle was 12.82, 72.69, 68.19, and 92.25 U / mg prot, respectively. Compared to the control reactor, the relative abundance of Nir enzyme in the reduced manganese reactor, reduced iron reactor, and reduced manganese / reduced iron reactor increased by 5.67, 5.55, and 7.20 times, respectively. The relative abundance of Nir enzyme in the control reactor, reduced manganese reactor, reduced iron reactor, and reduced manganese / reduced iron reactor during the second cycle was 13.09, 89.09, 74.23, and 126.48 U / mg prot, respectively. Compared to the control reactor, the relative abundance of Nir enzyme in the reduced manganese reactor, reduced iron reactor, and reduced manganese / reduced iron reactor increased by 6.81, 5.677, and 9.66 times, respectively. Figure 12As shown in (b), the relative abundance of Nar enzymes in the control reactor, reduced manganese reactor, reduced iron reactor, and reduced manganese / reduced iron reactor during the first cycle were 141.55, 433.64, 423.21, and 455.90 U / mg prot, respectively. Compared to the control reactor, the relative abundance of Nar enzymes in the reduced manganese reactor, reduced iron reactor, and reduced manganese / reduced iron reactor increased by 3.06, 2.99, and 3.22 times, respectively. The relative abundance of Nar enzymes in the control reactor, reduced manganese reactor, reduced iron reactor, and reduced manganese / reduced iron reactor during the second cycle were 221.72, 410.08, 407.91, and 513.04 U / mg prot, respectively. Compared to the control reactor, the relative abundance of Nar enzymes in the reduced manganese reactor, reduced iron reactor, and reduced manganese / reduced iron reactor increased by 1.85, 1.83, and 2.31 times, respectively.

[0092] III. The microbial community structure of the dual-membrane micro-ecosystem of the denitrification ecological reaction chamber obtained by the present invention.

[0093] Following the methods and steps described in Examples 1, 2, and 5, a dual-membrane micro-ecosystem for iron-based denitrification and nitrogen removal in a reactor was constructed. Microbial samples were collected from water and sediment at the end of the first and second reaction cycles, and stored at -80°C. Metagenomic sequencing was then performed.

[0094] The microbial community structure 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 reaction cycles is as follows: Figure 13 As shown. Figure 13As shown in (a), Proteobacteria, Actinobacteria, Bacteroidota, Planctomycetota, and Firmicutes were the dominant phyla in the water. At the end of the first cycle, the abundance of Proteobacteria in the control reactor, reduced manganese reactor, reduced iron reactor, and reduced manganese / reduced iron reactor were 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 were 92.66%, 67.14%, 64.41%, and 72.09%, respectively. At the end of the first cycle, the abundance of Actinobacteria in the manganese powder reactor was 4.82%, while the abundance of Actinobacteria in the control reactor was 0.57%. The abundance of *Bacteroidota* at the end of the first cycle in the control reactor, reduced manganese reactor, reduced iron reactor, and reduced manganese / reduced iron reactor were 15.24%, 13.87%, 6.71%, and 4.95%, respectively. At the end of the second cycle, the abundance of *Bacteroidota* in the control reactor, reduced manganese reactor, reduced iron reactor, and reduced manganese / reduced iron reactor were 4.14%, 10.83%, 4.47%, and 6.12%, respectively. The abundance of *Firmicutes* at the end of the first cycle in the reduced manganese reactor, reduced iron reactor, and reduced manganese / reduced iron reactor were all below 1%, while the abundance of *Firmicutes* in the control reactor was 1.61%. Furthermore, 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. Figure 13As shown in (b), Proteobacteria, Actinobacteria, Chloroflexi, Bacteroidota, Acidobacteria, Planctomycetota, and Nitrospirae were the dominant phyla in the sediments of both the control reactor and the manganese / iron-enhanced reactor. The operation of the reactors had minimal impact on the microorganisms in the sediments, and the microbial composition of the sediment samples from each system was similar at the phylum level, with no significant changes in the dominance of the dominant phyla. The abundance of Proteobacteria was approximately 57.19–71.00%, Chloroflexi was approximately 5.78–8.83%, Actinobacteria was approximately 5.99–8.11%, Bacteroidota was approximately 1.89–10.93%, Acidobacteria was approximately 5.78–10.22%, Firmicutes was approximately 0.54–1.17%, Planctomycetota was approximately 2.11–5.41%, and Nitrospirae was approximately 2.79–4.46%.

[0095] Heat maps of the microbial community at the family level at the end of the first and second cycles of the control group and the manganese / iron enhanced reactor water and sediment are shown below. Figure 14 As shown. Figure 14 As shown in (a), in the water sample, 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. Figure 14As shown in (b), Bacillaceae and Moraxellaceae were the dominant bacterial families in the control reactor in the sediment samples. Comamonadaceae, Methylophilaceae, Sphingomonadaceae, Azospirillaceae, Thiobacillaceae, Nocardiaceae, Rhodobacteraceae, Steroidobacteraceae, and Pseudomonadaceae were the dominant bacterial families in the reactor with added manganese / iron inorganic electron donors. It should be noted that the dominant bacterial families Steroidobacteraceae and Comamonadaceae are bacterial families with both denitrification and iron-manganese reduction functions, which verifies the feasibility of the method.

[0096] III. The role of the denitrification denitrification ecological reaction chamber dual-membrane micro-ecosystem constructed in Examples 2 and 4 of the present invention in pollutant removal in the aquatic environment.

[0097] Water and sediment samples were collected from the Jinpen Reservoir in Xi'an City. The water samples were collected from the surface water at the center of the reservoir. Sediments were collected using a grab bucket sludge collector. Both water and sediment samples were stored in sterile collection bottles in a portable refrigerator at 4°C and transported back to the laboratory within 48 hours. KNO3 and sodium acetate were added to the water samples to adjust the NO3 concentration. − -N and COD concentrations, after adjustment the carbon-to-nitrogen ratio of the water body to approximately 1, and the initial NO3 concentration. − -N concentration is 5 mg / L.

[0098] A 5 L glass reactor was used, with dimensions of 130 mm inner diameter × 376.7 mm column height. Before the experiment, a manganese-based denitrification denitrification ecological reaction chamber dual-membrane micro-ecosystem and a composite manganese-based denitrification denitrification ecological reaction chamber dual-membrane micro-ecosystem were constructed according to the methods and steps in Examples 2 and 4. The reactor groups were set as follows: (1) sediment + overlying water; (2) sediment + overlying water + manganese-based denitrification denitrification ecological reaction chamber dual-membrane micro-ecosystem; (3) sediment + overlying water + composite manganese-based denitrification denitrification ecological reaction chamber dual-membrane micro-ecosystem.

[0099] The aforementioned metallic manganese was purchased from Henan Boyuan Water Purification Materials Co., Ltd. Specifically, the amount of sediment added to the reactor was 250 mL, the amount of inorganic electron donor packing material in the manganese-based denitrification ecological reaction chamber double-membrane micro-ecosystem was 5 g / L, the amount of inorganic electron donor packing material in the composite manganese-based denitrification ecological reaction chamber double-membrane micro-ecosystem was 5 g / L, and 2.5 g each of metallic manganese and activated carbon packing material were added.

[0100] All reactors were aerated using oxygen pumps during operation. Source water was added to the reactors via siphon along the reactor wall. The reactors operated for five cycles totaling 120 days, with each cycle lasting 20 days. Total nitrogen (TN) and nitrogen oxides (NO3) were measured every two days. — N, NO2 — N, NH4 + -N, COD Mn TP concentration, set up 3 replicates.

[0101] TN, NO3 — N, NO2 — N and NH4 + -N changes over time as follows Figure 15 and Figure 16 As shown. Within five reaction cycles, as... Figure 15 As shown, the NO3 content in the control reactor without a micro-ecosystem... − -N concentration decreased from 5.26 mg / L to 5.08 mg / L–4.97 mg / L. (NO3 concentration in the control reactor was also lower.) − The nitrogen (TN) removal rates were 8.88%, 15.86%, 13.86%, 13.66%, and 12.27%, respectively. In the control reactor, the TN concentration decreased from 5.71 mg / L to 5.18 mg / L–5.04 mg / L. This was because the initial TN concentration was slightly higher than that of NO3. − -N, the TN removal rates during reactor operation were 22.84%, 20.23%, 20.23%, 20.24%, and 14.54%, respectively. For example... Figure 16 As shown in (a), the manganese-based denitrification denitrification ecological reaction chamber dual-membrane micro-ecosystem reactor NO3 − -N concentration decreased from 6.36 mg / L to 0.25 mg / L–1.02 mg / L, with removal rates of 93.13%, 95.85%, 94.32%, 84.53%, and 82.57%, respectively; TN concentration decreased from 6.48 mg / L to 0.40 mg / L–1.21 mg / L, with removal rates of 93.88%, 93.56%, 93.57%, 93.56%, and 80.13%, respectively. Figure 16 As shown in (b), the composite manganese-based denitrification and nitrogen removal ecological reaction chamber dual-membrane micro-ecosystem reactor NO3 −The nitrogen (N) concentration decreased from 6.14 mg / L to 0.14 mg / L and 0.91 mg / L, with removal rates of 94.67% and 94.70%, respectively; the nitrogen (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. No significant accumulation of ammonia nitrogen was observed, while trace amounts of nitrite nitrogen accumulated in all five cycles, which were subsequently rapidly reduced.

[0102] The dual-membrane micro-ecosystem of the denitrification and nitrogen removal ecological reaction chamber constructed in this invention has a positive effect on COD. Mn Its removal ability and removal effect are as follows Figure 17 As shown. Within five reaction cycles, as... Figure 17 As shown in (a), the control reactor of the dual-membrane micro-ecosystem without denitrification denitrification ecological reaction chamber has a COD Mn The concentration decreased from 5.39 mg / L to 3.24 mg / L–4.11 mg / L, with removal rates of 39.85%, 29.22%, 25.48%, 26.73%, and 23.82%, respectively. Figure 17 As shown in (b), the COD of the manganese-based denitrification denitrification ecological reaction chamber dual-membrane micro-ecosystem is... Mn The concentration decreased from 5.40 mg / L to 0.835 mg / L–1.01 mg / L, with removal rates of 83.50%, 83.49%, 83.97%, 84.17%, and 82.99%, respectively. The COD removal efficiency of the composite manganese-based denitrification ecological reaction chamber with dual-membrane micro-ecosystem was [not specified]. Mn The concentration decreased from 5.41 mg / L to 0.60 mg / L to 0.84 mg / L, with removal rates of 71.39%, 88.91%, 86.82%, 88.31%, and 86.03%, respectively.

[0103] The denitrification and nitrogen removal ecological reaction chamber dual-membrane micro-ecosystem constructed in this invention exhibits the following removal capacity and effect on TP: Figure 18As shown in the figure, over five reaction cycles, the TP concentration in the control reactor of the non-denitrification denitrification ecological reactor with dual membrane micro-ecosystem decreased from 0.34 mg / L to 0.19 mg / L–0.27 mg / L, with removal rates of 36.43%, 32.49%, 43.32%, 25.27%, and 21.66%, respectively. In the manganese-based denitrification denitrification ecological reactor with dual membrane micro-ecosystem, the TP concentration decreased from 0.34 mg / L to 0.03 mg / L–0.12 mg / L, with removal rates of 89.07%, 90.25%, 86.64%, 68.59%, and 64.98%, respectively. In the composite manganese-based denitrification denitrification ecological reactor with dual membrane micro-ecosystem, the TP concentration decreased from 0.34 mg / L to 0.03 mg / L–0.09 mg / L, with removal rates of 89.08%, 90.25%, 86.64%, 75.82%, and 72.20%, respectively.

[0104] Although preferred embodiments of the invention have been described, those skilled in the art, once they have learned the basic inventive concept, can make other changes and modifications to these embodiments.

[0105] Obviously, those skilled in the art can make various modifications and variations to this invention without departing from its spirit and scope. Therefore, if these modifications and variations fall within the scope of the claims of this invention and their equivalents, this invention also intends to include these modifications and variations.

Claims

1. A method for constructing a dual-membrane micro-ecosystem for water source denitrification ecological reaction chamber, characterized in that, Includes the following steps: Inorganic electron donor packing material with a volume fraction of 10%–40% was added to the reactor. An alternating aerobic / anaerobic environment was created through intermittent aeration. The aeration time to interval time ratio during intermittent aeration was 10 h–12 h:12 h. Reservoir source water was introduced intermittently. During the intermittent water inlet process, the hydraulic retention time in the reactor was 3 d–7 d, and the water inlet time was 1 h–2 h. The intermittent water inlet step was repeated 3 to 5 times. An aerobic denitrification enhanced denitrification part was generated on the surface of the inorganic electron donor packing material, and a denitrification denitrification ecological reaction chamber dual-membrane micro-ecosystem was obtained. The inorganic electron donor packing is a mineral packing or a composite packing of mineral packing and inorganic carbon; The mineral packing material is metallic iron packing material, metallic manganese packing material, or a composite packing material of metallic iron and metallic manganese. The mineral filler and inorganic carbon composite filler are made by mixing mineral filler and inorganic carbon in a mass ratio of 1-5:1-5. The water source denitrification ecological reaction chamber's dual-membrane micro-ecosystem has both denitrification and phosphorus removal functions.

2. The method for constructing the dual-membrane micro-ecosystem of the water source denitrification ecological reaction chamber according to claim 1, characterized in that, The inorganic carbon is activated carbon or biochar.

3. The method for constructing the dual-membrane micro-ecosystem of the water source denitrification ecological reaction chamber according to claim 1, characterized in that, The preparation process of the mineral filler and inorganic carbon composite filler is as follows: the inorganic carbon and mineral filler are washed sequentially with distilled water and H2SO4 solution with a volume fraction of 10% to 20%, then dried and stirred to obtain the mineral filler and inorganic carbon composite filler.

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

5. The dual-membrane micro-ecosystem of water source denitrification ecological reaction chamber constructed by the construction method according to any one of claims 1 to 4, characterized in that, This includes inorganic electron donors and the aerobic denitrification enhanced nitrogen removal process formed on their surfaces.

6. The application of the dual-membrane micro-ecosystem of the water source denitrification ecological reaction chamber as described in claim 5 in water treatment, characterized in that, The denitrification and nitrogen removal ecological reaction chamber dual-membrane micro-ecosystem is used for nitrogen removal in the water source reservoir; the water treatment also includes reducing the concentration of COD and total phosphorus in the water; increasing the total ATP concentration, ETSA concentration, relative activity of complex I and complex III, Nar enzyme abundance and Nir enzyme abundance of microorganisms in the water.

7. The application of the dual-membrane micro-ecosystem of the water source denitrification ecological reaction chamber according to claim 6 in water treatment, characterized in that, The denitrification process involves reducing the levels of total nitrogen, nitrate, nitrite, and ammonia in the aquatic environment.

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