Wastewater treatment method and device based on anaerobic ammonia oxidation bacteria biomass balance and electronic equipment

Abstract

The present application relates to the technical field of wastewater treatment, and particularly relates to a wastewater treatment method and device based on anaerobic ammonia oxidation bacteria biomass balance and electronic equipment, the wastewater treatment method comprising: obtaining a growth efficiency correction factor of anaerobic ammonia oxidation bacteria; obtaining a denitrification load target design value, a hydraulic retention time target design value and a proportion target design value of anaerobic ammonia oxidation bacteria in a biological phase of a reactor; calculating a minimum threshold value of influent volatile suspended solid concentration of wastewater to be treated according to the growth efficiency correction factor, the denitrification load target design value, the hydraulic retention time target design value and the proportion target design value of anaerobic ammonia oxidation bacteria in the biological phase; and determining working parameters of a pretreatment unit of the reactor according to the minimum threshold value of the influent volatile suspended solid concentration. Thus, the net growth of anaerobic ammonia oxidation bacteria can be ensured to be sufficient to offset the biomass loss caused by physical flushing, and functional collapse caused by excessive loss of biomass can be avoided.

Description

Technical Field

[0001] This invention relates to the field of wastewater treatment technology, specifically to a wastewater treatment method, apparatus, and electronic equipment based on the biomass balance of anaerobic ammonia-oxidizing bacteria. Background Technology

[0002] Anammox is a low-energy and highly efficient nitrogen removal process with significant application prospects in treating wastewater with low C / N ratios and high ammonia nitrogen. Since its discovery in the 1990s, over 100 full-scale anammox engineering plants have been built globally. Compared to traditional nitrification-denitrification processes, anammox requires no additional carbon source and has lower aeration energy consumption, making it a crucial technological pathway for achieving carbon neutrality in wastewater treatment plants. However, anammox bacteria (AnAOB) are typical slow-growing autotrophic microorganisms with a doubling time of 10-20 days, directly leading to excessively long start-up cycles and difficulties in biomass enrichment in anammox reactors. To address this challenge, related technologies typically employ reactors with strong biological retention capabilities, such as upflow anaerobic sludge blanket (UASB), sequencing batch reactors (SBR), and membrane bioreactors (MBR). Despite significant progress in anaerobic ammonia oxidation technology, the long-term operational stability of systems treating complex, high-concentration organic wastewaters such as pig farm wastewater and landfill leachate still faces serious challenges. Current research primarily focuses on "soluble inhibitors," with numerous publications and patents reporting on nitrite (NO2). - Studies have investigated the inhibitory effects of chemical substances such as free ammonia (FA), salinity, heavy metals (e.g., Cu, Ni, Zn), sulfides, and antibiotics on anaerobic ammonia oxidation activity. These studies suggest that controlling these chemical parameters within extremely low thresholds, such as 0.5–10 mg / L, ensures stable system operation. However, practical engineering experience shows that even when chemical parameters are fully met, irreversible system failure can still occur. Summary of the Invention

[0003] This invention provides a wastewater treatment method, apparatus, electronic equipment, storage medium, and program product based on anaerobic ammonia oxidation bacteria biomass balance, in order to solve the problem of poor stability of anaerobic ammonia oxidation technology when denitrifying wastewater.

[0004] In a first aspect, the present invention provides a wastewater treatment method based on the biomass balance of anaerobic ammonia oxidizing bacteria. The method includes the following steps: obtaining a growth efficiency correction factor η for anaerobic ammonia oxidizing bacteria; obtaining the target design value of the denitrification load NRR, the target design value of the hydraulic retention time HRT, and the target design value X1 of the proportion of anaerobic ammonia oxidizing bacteria in the biological phase of the reactor; calculating the minimum threshold of the influent volatile suspended solids concentration of the wastewater to be treated based on the growth efficiency correction factor η, the target design value of the denitrification load NRR, the target design value of the hydraulic retention time HRT, and the target design value X1 of the proportion of anaerobic ammonia oxidizing bacteria in the biological phase; and determining the operating parameters of the reactor pretreatment unit based on the minimum threshold of the influent volatile suspended solids concentration.

[0005] The wastewater treatment method based on anaerobic ammonia oxidizing bacteria biomass balance provided by this invention introduces a growth efficiency correction factor and combines parameters such as denitrification load and hydraulic retention time to construct a calculation model for the minimum threshold of influent volatile suspended solids concentration. This enables precise quantitative control of biomass loss in the anaerobic ammonia oxidation system. Furthermore, by determining the operating parameters through the minimum threshold of influent volatile suspended solids concentration, it ensures that the net growth of anaerobic ammonia oxidizing bacteria is sufficient to offset the biomass loss caused by physical flushing, avoiding functional collapse due to excessive biomass loss, and significantly improving the operational stability of the anaerobic ammonia oxidation system when treating wastewater with high suspended solids.

[0006] In some optional embodiments, obtaining the target design values ​​for the denitrification load (NRR), hydraulic retention time (HRT), and the proportion of anaerobic ammonia-oxidizing bacteria in the biological phase (X1) of the reactor includes: obtaining the influent nitrogen concentration (C) in the wastewater to be treated. N ; Obtain the nitrogen removal percentage Z from the anaerobic ammonia oxidation pathway; Based on the first constraint, according to the influent nitrogen concentration C N The proportion of nitrogen removal via the anaerobic ammonia oxidation pathway (Z) was used to screen the initial values ​​of the nitrogen removal load and hydraulic retention time, obtaining a data set that met the first constraint condition. This data set included the initial design values ​​of the nitrogen removal load and hydraulic retention time. The substrate consumption efficiency (q) of the anaerobic ammonia oxidizing bacteria was then obtained. s ; Obtain the suspended sludge concentration (MLVSS) in the reactor and the percentage (X2) of anaerobic ammonia-oxidizing bacteria in the biological phase of the wastewater to be treated; Based on the second constraint, utilize the substrate consumption efficiency q s The initial design value of denitrification load was screened by measuring the suspended sludge concentration (MLVSS) and the proportion of anaerobic ammonia oxidizing bacteria in the biological phase of the wastewater to be treated (X2). The target design value of denitrification load (NRR) and the target design value of the proportion of anaerobic ammonia oxidizing bacteria in the biological phase (X1) were determined. The initial design value of hydraulic retention time (HRT) paired with the target design value of denitrification load (NRR) in the data set was extracted and determined as the target design value of hydraulic retention time (HRT).

[0007] This implementation method introduces multi-dimensional parameters such as influent nitrogen concentration, denitrification ratio, and substrate consumption efficiency, and combines dual constraints to screen and optimize the design values ​​step by step, thereby achieving a coordinated match between denitrification load, hydraulic retention time, and microbial ratio.

[0008] In some optional implementations, calculating the minimum threshold for influent volatile suspended solids concentration of the wastewater to be treated based on the growth efficiency correction factor η, the target design value of denitrification load NRR, the target design value of hydraulic retention time HRT, and the target design value X1 of the proportion of anaerobic ammonia oxidizing bacteria in the biological phase includes: calculating the basic threshold using a preset basic threshold calculation formula based on the growth efficiency correction factor η, the target design value of denitrification load NRR, the target design value of hydraulic retention time HRT, and the target design value X1 of the proportion of anaerobic ammonia oxidizing bacteria in the biological phase; determining the biomass yield of other bacteria based on the type of reactor; and correcting the basic threshold using the biomass yield of other bacteria to obtain the minimum threshold for influent volatile suspended solids concentration.

[0009] This implementation method uses a preset basic threshold calculation formula and adjusts the biomass yield of other bacteria based on the reactor type to obtain a more accurate minimum threshold for the concentration of volatile suspended solids in the influent. This not only improves the accuracy of threshold calculation but also effectively adapts to different reactor operating conditions, enhances the system's tolerance to fluctuations in influent water quality, and ensures the stable operation of the anaerobic ammonia oxidation process.

[0010] In some optional embodiments, after calculating the minimum threshold for the influent volatile suspended solids concentration of the wastewater to be treated based on the growth efficiency correction factor η, the target design value of denitrification load NRR, the target design value of hydraulic retention time HRT, and the target design value of the proportion of anaerobic ammonia oxidizing bacteria in the biological phase X1, the method further includes: obtaining the minimum product volatile suspended solids concentration of the reactor pretreatment unit; determining whether the minimum threshold for the influent volatile suspended solids concentration is greater than the minimum product volatile suspended solids concentration; and when the minimum threshold for the influent volatile suspended solids concentration is less than or equal to the minimum product volatile suspended solids concentration, after adjusting the suspended sludge concentration MLVSS of the reactor, recalculating the minimum threshold for the influent volatile suspended solids concentration.

[0011] This implementation method compares the calculated minimum threshold for influent volatile suspended solids concentration with the minimum achievable suspended solids concentration in the reactor's product water. This effectively verifies whether the theoretically calculated values ​​meet the actual operational requirements of the system under current conditions. If the theoretical threshold is lower than the actual treatment limit, the sludge concentration, the target design value for nitrogen removal load (NRR), the target design value for hydraulic retention time (HRT), and the target design value for the proportion of anaerobic ammonia-oxidizing bacteria in the biological phase (X1) are adjusted and recalculated to ensure the final influent water quality parameters are practically operable.

[0012] In some optional implementations, determining the operating parameters for treating wastewater using anaerobic ammonia oxidizing bacteria based on the minimum threshold of influent volatile suspended solids concentration includes: obtaining a preset mapping matrix, which characterizes the quantitative relationship between solid-liquid separation process parameters and the corresponding effluent suspended solids concentration; and using the minimum threshold of influent volatile suspended solids concentration to search in the mapping matrix to obtain the operating parameters of the reactor pretreatment unit.

[0013] This implementation method establishes a linkage mechanism between a preset mapping matrix and the minimum threshold of volatile suspended solids in the influent, which can accurately determine the operating parameters of the pretreatment unit, thereby ensuring that the system always operates within a safe biomass balance boundary.

[0014] In some optional embodiments, before determining the operating parameters of the reactor pretreatment unit based on the minimum threshold of the influent volatile suspended solids concentration, the method further includes: obtaining the actual product water suspended solids concentration of the reactor; determining whether the actual product water suspended solids concentration is less than the minimum threshold of the influent volatile suspended solids concentration; and when the actual product water suspended solids concentration is greater than or equal to the minimum threshold of the influent volatile suspended solids concentration, performing the step of determining the operating parameters of the reactor pretreatment unit based on the minimum threshold of the influent volatile suspended solids concentration.

[0015] This implementation method can dynamically verify whether the current water quality meets the influent requirements by comparing the actual suspended solids concentration in the produced water with the minimum threshold in the influent in real time. The pretreatment parameters are only re-determined when the actual suspended solids concentration in the produced water does not meet the standard. This feedback mechanism of on-demand control effectively avoids redundant adjustments and improves the system's operating efficiency and control accuracy.

[0016] Secondly, the present invention also provides a wastewater treatment device based on the biomass balance of anaerobic ammonia oxidizing bacteria. The device includes a first acquisition module, a second acquisition module, a calculation module, and a working parameter determination module. The first acquisition module is used to acquire the growth efficiency correction factor η of anaerobic ammonia oxidizing bacteria. The second acquisition module is used to acquire the target design value of the denitrification load NRR, the target design value of the hydraulic retention time HRT, and the target design value X1 of the proportion of anaerobic ammonia oxidizing bacteria in the biological phase of the reactor. The calculation module is used to calculate the minimum threshold of the influent volatile suspended solids concentration of the wastewater to be treated based on the growth efficiency correction factor η, the target design value of the denitrification load NRR, the target design value of the hydraulic retention time HRT, and the target design value X1 of the proportion of anaerobic ammonia oxidizing bacteria in the biological phase. The working parameter determination module is used to determine the working parameters of the reactor pretreatment unit based on the minimum threshold of the influent volatile suspended solids concentration.

[0017] Thirdly, the present invention provides an electronic device, including a memory and a processor, which are interconnected. The memory stores computer instructions, and the processor executes the computer instructions to perform the wastewater treatment method based on the biomass balance of anaerobic ammonia oxidizing bacteria described in the first aspect or any corresponding embodiment.

[0018] Fourthly, the present invention provides a computer-readable storage medium storing computer instructions for causing a computer to perform the wastewater treatment method based on anaerobic ammonia-oxidizing bacteria biomass balance described in the first aspect or any corresponding embodiment.

[0019] Fifthly, the present invention provides a computer program product, including computer instructions for causing a computer to execute the wastewater treatment method based on anaerobic ammonia-oxidizing bacteria biomass balance described in the first aspect or any corresponding embodiment thereof. Attached Figure Description

[0020] To more clearly illustrate the specific embodiments of the present invention or the technical solutions in the prior art, the drawings used in the description of the specific embodiments or the prior art will be briefly introduced below. Obviously, the drawings described below are some embodiments of the present invention. For those skilled in the art, other drawings can be obtained from these drawings without creative effort.

[0021] Figure 1 This is a schematic diagram illustrating an application scenario of an embodiment of the present invention; Figure 2 This is a schematic diagram of the biomass balance theory of anaerobic ammonia oxidizing bacteria in a reactor according to the present invention; Figure 3 This is a first flow chart of a wastewater treatment method based on the biomass balance of anaerobic ammonia oxidizing bacteria according to an embodiment of the present invention; Figure 4 This is a second flow chart of a wastewater treatment method based on the biomass balance of anaerobic ammonia oxidizing bacteria according to an embodiment of the present invention; Figure 5 This is a schematic diagram illustrating the derivation process of the biomass balance point of anaerobic ammonia-oxidizing bacteria in the reactor according to an embodiment of the present invention; Figure 6 This is a schematic diagram of an example of a wastewater treatment method based on the biomass balance of anaerobic ammonia oxidizing bacteria according to an embodiment of the present invention; Figure 7 This is a schematic flow diagram of a wastewater treatment method based on the biomass balance of anaerobic ammonia oxidizing bacteria according to an embodiment of the present invention. Figure 8 This is a schematic diagram illustrating the growth of anaerobic ammonia-oxidizing bacteria during the water distribution stage and the actual aquaculture wastewater stage according to an embodiment of the present invention. Figure 9 This is a schematic diagram showing the change in the proportion of anaerobic ammonia oxidizing bacteria in the biological phase in a 1L laboratory-scale anaerobic ammonia oxidation reactor according to an embodiment of the present invention. Figure 10 This is a schematic diagram showing the proportion of anaerobic ammonia-oxidizing bacteria at different stages of water inlet in a pilot-scale reactor according to an embodiment of the present invention. Figure 11 This is a schematic diagram illustrating the differences in net growth of anaerobic ammonia oxidizing bacteria under different influent types and influent SS conditions according to an embodiment of the present invention. Figure 12 This is a structural block diagram of a wastewater treatment device based on the biomass balance of anaerobic ammonia oxidizing bacteria according to an embodiment of the present invention; Figure 13 This is a schematic diagram of the structure of an electronic device according to an embodiment of the present invention. Detailed Implementation

[0022] To make the objectives, technical solutions, and advantages of the embodiments of the present invention clearer, the technical solutions of the embodiments of the present invention will be clearly and completely described below with reference to the accompanying drawings. Obviously, the described embodiments are only some embodiments of the present invention, not all 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.

[0023] It is understood that before using the technical solutions disclosed in the various embodiments of the present invention, users should be informed of the types, scope of use, and usage scenarios of the personal information involved in the present invention and their authorization should be obtained in accordance with relevant laws and regulations through appropriate means.

[0024] The terms "first" and "second" are used for descriptive purposes only and should not be construed as indicating or implying relative importance or implicitly specifying the number of technical features indicated. Thus, a feature defined as "first" or "second" may explicitly or implicitly include one or more of that feature. In the description of this invention, "a plurality of" means two or more, unless otherwise explicitly specified.

[0025] As an optional application scenario of this invention, such as Figure 1 As shown, the system may include at least one terminal device and at least one server. Figure 1 The system is illustrated in the example, which includes a computer 101, a mobile terminal 102, and a server 103, and the terminal devices such as the computer 101 and the mobile terminal 102 are connected to the server 103 through a network 110.

[0026] Specifically, the terminal device can be a smartphone, tablet, laptop, PDA, desktop computer, game console, smart TV, smart wearable device, in-vehicle terminal, VR (Virtual Reality) device, AR (Augmented Reality) device, etc. Server 103 can be a standalone physical server, a server cluster, a distributed system, or a cloud server providing cloud services. Network 110 can be a wired or wireless network, examples of which include, but are not limited to, the Internet, corporate intranet, local area network, wide area network, mobile communication network, and combinations thereof.

[0027] Studies have revealed significant shortcomings in the design and operation research of current anaerobic ammonia oxidation systems. First, existing research overemphasizes the chemical toxicity of soluble inhibitors (such as ammonia nitrogen and nitrite nitrogen), generally neglecting the physical dilution and scouring of biomass caused by influent suspended solids. This can lead to "functional collapse" of the system even when chemical indicators are normal. Second, traditional models fail to account for the significant decrease in growth efficiency in complex wastewater. For example, under pig farm wastewater conditions, growth efficiency is only 50% of the theoretical value, resulting in overly optimistic biomass proliferation predictions.

[0028] The stability of anaerobic ammonium oxidation systems is largely limited by the biomass balance at the physical level. For example... Figure 2 As shown, on the one hand, under toxic conditions, there is a balance between the maintenance energy required for anaerobic ammonia oxidizing bacteria to maintain their physiological and biochemical activities and the energy required for growth, leading to changes in growth efficiency. On the other hand, the shock of influent suspended solids (SS) concentration exacerbates physical loss, while biomass retention capacity is affected by factors such as reactor type and carrier type. When the "growth" and "loss" of microorganisms reach an equilibrium point, the system can maintain a stable biomass, which is the key to ensuring the long-term stable operation of the anaerobic ammonia oxidation process.

[0029] When treating wastewater with high suspended solids, the suspended solids in the influent continuously dilute and erode the activated sludge or biofilm, leading to a long-term physical loss of anaerobic ammonia oxidizing bacteria biomass. The system collapse is essentially due to the inability of the extremely slow net growth of anaerobic ammonia oxidizing bacteria to compensate for the biomass loss caused by physical erosion. This is particularly true when treating complex systems such as pig farm wastewater, where the presence of unknown inhibitory factors in the wastewater significantly reduces the effective growth efficiency of anaerobic ammonia oxidizing bacteria, further exacerbating the biomass loss effect.

[0030] Based on this, according to an embodiment of the present invention, a wastewater treatment method based on anaerobic ammonia-oxidizing bacteria biomass balance is provided. It should be noted that the steps shown in the flowchart in the accompanying drawings can be executed in a computer system such as a set of computer-executable instructions. Furthermore, although a logical order is shown in the flowchart, in some cases, the steps shown or described may be executed in a different order than that shown here.

[0031] This embodiment provides a wastewater treatment method based on anaerobic ammonia-oxidizing bacteria biomass balance, which can be used on the aforementioned mobile terminals, such as mobile phones and tablets. Figure 3 This is a first flow chart of a wastewater treatment method based on anaerobic ammonia-oxidizing bacteria biomass balance according to an embodiment of the present invention, as shown below. Figure 3 As shown, the process includes the following steps: Step S301: Obtain the growth efficiency correction factor η of anaerobic ammonia oxidizing bacteria.

[0032] The growth efficiency correction factor η is a key parameter for measuring the proliferation efficiency of anaerobic ammonia oxidizing bacteria under actual operating conditions. Its calculation formula is defined as: η = (Net growth of anaerobic ammonia oxidizing bacteria + Effluent loss of anaerobic ammonia oxidizing bacteria) / Theoretical growth of anaerobic ammonia oxidizing bacteria. For example, the theoretical growth of anaerobic ammonia oxidizing bacteria is taken as the standard value of 0.05569 g VS / g N.

[0033] To accurately obtain the data in the above formulas, it is necessary to measure the net growth rate of anaerobic ammonia oxidizing bacteria and the effluent loss. The net growth rate is obtained by calculating the difference in anaerobic ammonia oxidizing bacteria biomass in the reactor at the start and end points of the experiment. Specifically, the suspended sludge concentration and the proportion of anaerobic ammonia oxidizing bacteria in the biological phase are measured at the start and end points, respectively. These two values ​​are multiplied to obtain the anaerobic ammonia oxidizing bacteria biomass at each stage, and the difference is the net growth rate. The effluent loss is determined by recording the cumulative effluent volume during the experimental period and obtaining the average concentration of volatile suspended solids in the effluent from at least three random samples within the period. Simultaneously, the arithmetic mean of the proportion of anaerobic ammonia oxidizing bacteria from the start to the end point is used as the average proportion of anaerobic ammonia oxidizing bacteria in the effluent. Finally, the effluent loss is obtained by multiplying the cumulative effluent volume, the average proportion of anaerobic ammonia oxidizing bacteria in the effluent, and the average concentration of volatile suspended solids in the effluent.

[0034] In practical applications, the value of the growth efficiency correction factor η varies depending on water quality conditions and bacterial species. Under standard laboratory artificial water preparation conditions, η is 1.0; in industrial wastewater containing inhibitory factors, the value of η typically ranges from 0 to 1. In the pig farm wastewater system addressed in this embodiment, the anaerobic ammonia-oxidizing bacteria Ca... Kuenenia The specific value of η for bacteria is 0.5.

[0035] Step S302: Obtain the target design value of denitrification load NRR, the target design value of hydraulic retention time HRT, and the target design value of the proportion of anaerobic ammonia oxidizing bacteria in the biological phase X1 of the reactor.

[0036] Step S303: Calculate the minimum threshold for the concentration of volatile suspended solids in the influent of the wastewater to be treated based on the growth efficiency correction factor η, the target design value of denitrification load NRR, the target design value of hydraulic retention time HRT, and the target design value of the proportion of anaerobic ammonia oxidizing bacteria in the biological phase X1.

[0037] Step S304: Determine the operating parameters of the reactor pretreatment unit based on the minimum threshold of volatile suspended solids concentration in the influent.

[0038] The wastewater treatment method based on anaerobic ammonia oxidizing bacteria biomass balance provided in this embodiment introduces a growth efficiency correction factor and combines parameters such as denitrification load and hydraulic retention time to construct a calculation model for the minimum threshold of influent volatile suspended solids concentration. This enables precise quantitative control of biomass loss in the anaerobic ammonia oxidation system. Furthermore, by determining the operating parameters through the minimum threshold of influent volatile suspended solids concentration, it ensures that the net growth of anaerobic ammonia oxidizing bacteria is sufficient to offset the biomass loss caused by physical flushing, avoiding functional collapse due to excessive biomass loss, and significantly improving the operational stability of the anaerobic ammonia oxidation system when treating wastewater with high suspended solids.

[0039] This embodiment provides a wastewater treatment method based on anaerobic ammonia-oxidizing bacteria biomass balance, which can be used on the aforementioned mobile terminals, such as mobile phones and tablets. Figure 4 This is a second flow chart of a wastewater treatment method based on anaerobic ammonia-oxidizing bacteria biomass balance according to an embodiment of the present invention, as shown below. Figure 4 As shown, the process includes the following steps: Step S401: Obtain the growth efficiency correction factor η of anaerobic ammonia oxidizing bacteria.

[0040] Step S402: Obtain the target design value of denitrification load NRR, the target design value of hydraulic retention time HRT, and the target design value of the proportion of anaerobic ammonia oxidizing bacteria in the biological phase X1 of the reactor.

[0041] In one optional embodiment, obtaining the target design value of denitrification load NRR, the target design value of hydraulic retention time HRT, and the target design value of the proportion of anaerobic ammonia oxidizing bacteria in the biological phase of the reactor includes the following steps S4021 to S4027.

[0042] Step S4021: Obtain the influent nitrogen concentration C in the wastewater to be treated. N .

[0043] Step S4022: Obtain the nitrogen removal rate Z of the anaerobic ammonia oxidation pathway.

[0044] Step S4023: Based on the first constraint, according to the influent nitrogen concentration CN and the proportion of nitrogen removal through the anaerobic ammonia oxidation pathway Z, the initial values ​​of the denitrification load and the initial values ​​of the hydraulic retention time are screened to obtain a data set that meets the first constraint. The data set includes the initial design values ​​of the denitrification load and the initial design values ​​of the hydraulic retention time.

[0045] For example, when anaerobic ammonia oxidizing bacteria can remove up to 88% of nitrogen, the first constraint is Z×NRR×HRT≤88%×C N .

[0046] Step S4024: Obtain the suspended sludge concentration MLVSS in the reactor and the percentage of anaerobic ammonia oxidizing bacteria in the biological phase of the wastewater to be treated (X2).

[0047] Specifically, based on the reactor type (such as UASB, SBR, MBR, etc.), operating conditions, and the characteristics of the selected biological carrier (such as material, porosity, and dosage), the suspended sludge concentration MLVSS of the reactor is set, and the proportion of anaerobic ammonia oxidizing bacteria in the biological phase of the wastewater to be treated is measured as X2.

[0048] Step S4025: Obtain the substrate consumption efficiency q of anaerobic ammonia oxidizing bacteria. s .

[0049] Specifically, substrate consumption efficiency q s The determination of nitrogen content was performed using a batch method. The experiment required at least three independent replicates, maintaining ideal kinetic conditions with nitrite and ammonia nitrogen concentrations between 10 and 80 mg N / L and a mass concentration ratio of 1.32 ± 0.2 to ensure sufficient substrate in the reaction system. During the 8-hour reaction cycle, samples were taken every 2 hours to measure the concentration changes of the three nitrogen compounds (ammonia nitrogen, nitrite nitrogen, and nitrate nitrogen). Linear regression analysis was performed with time on the x-axis and total nitrogen consumption on the y-axis to derive the denitrification rate slope k for the reaction stage. Finally, the measured suspended sludge concentration and the proportion of anaerobic ammonia-oxidizing bacteria in the biological phase were combined and substituted into formula q. s = k / (MLVSS × X2) calculates the substrate consumption efficiency for each group of experiments, and takes the arithmetic mean of the results of 3 experiments as the final calibration parameter under this condition.

[0050] Step S4026: Based on the second constraint, utilize the substrate consumption efficiency q sThe initial design value of denitrification load was screened by measuring the suspended sludge concentration (MLVSS) and the proportion of anaerobic ammonia oxidizing bacteria in the biological phase of the wastewater to be treated (X2), and the target design value of denitrification load (NRR) and the target design value of the proportion of anaerobic ammonia oxidizing bacteria in the biological phase (X1) were determined.

[0051] For example, the second constraint is Z × NRR ≤ (q s ×MLVSS×X1).

[0052] Step S4027: Extract the initial design value of hydraulic residence time that is paired with the target design value of denitrification load NRR from the data set, and determine it as the target design value of hydraulic residence time HRT.

[0053] In one optional implementation, after calculating the minimum threshold for the influent volatile suspended solids concentration of the wastewater to be treated based on the growth efficiency correction factor η, the target design value of denitrification load NRR, the target design value of hydraulic retention time HRT, and the target design value of the proportion of anaerobic ammonia oxidizing bacteria in the biological phase X1, the method further includes: obtaining the minimum product volatile suspended solids concentration of the reactor; determining whether the minimum threshold for the influent volatile suspended solids concentration is greater than the minimum product volatile suspended solids concentration; and when the minimum threshold for the influent volatile suspended solids concentration is less than or equal to the minimum product volatile suspended solids concentration, after adjusting the suspended sludge concentration MLVSS of the reactor, recalculating the minimum threshold for the influent volatile suspended solids concentration.

[0054] It should be noted that after adjusting the suspended sludge concentration in the reactor, the target design values ​​for denitrification load, hydraulic retention time, and the proportion of anaerobic ammonia oxidizing bacteria in the biological phase will also change.

[0055] Step S403: Calculate the minimum threshold for the concentration of volatile suspended solids in the influent of the wastewater to be treated based on the growth efficiency correction factor η, the target design value of denitrification load NRR, the target design value of hydraulic retention time HRT, and the target design value of the proportion of anaerobic ammonia oxidizing bacteria in the biological phase X1.

[0056] Figure 5 This paper demonstrates a calculation method based on the biomass balance of anaerobic ammonia oxidizing bacteria. The left side represents the total biomass yield of anaerobic ammonia oxidizing bacteria under unit volume (1 L) and single hydraulic retention time (HRT) conditions, which is jointly determined by the nitrogen removal load target design value (NRR), hydraulic retention time (HRT), growth efficiency correction factor (η), and theoretical yield coefficient of anaerobic ammonia oxidizing bacteria (0.05569). The right side summarizes the total loss of anaerobic ammonia oxidizing bacteria, which is composed of the growth of anaerobic ammonia oxidizing bacteria (Y_AnAOB), the growth of other bacteria (Y_others), and the influent volatile suspended solids (C). VSS_inThe physical losses caused by these factors jointly determine the outcome.

[0057] By establishing the mass balance equation of total biomass production = total biomass loss, the equilibrium point condition formula for the concentration of volatile suspended solids in the influent can be derived: C VSS_in = (1-X1) / X1×Z×NRR×HRT×0.05569×η-Y_others.

[0058] In one optional implementation, the minimum threshold for the influent volatile suspended solids concentration of the wastewater to be treated is calculated based on the growth efficiency correction factor η, the target design value of denitrification load NRR, the target design value of hydraulic retention time HRT, and the target design value of the proportion of anaerobic ammonia oxidizing bacteria in the biological phase X1, including steps S4031 to S4033.

[0059] Step S4031: Calculate the basic threshold using the preset basic threshold calculation formula based on the growth efficiency correction factor η, the target design value of denitrification load NRR, the target design value of hydraulic retention time HRT, and the target design value of the proportion of anaerobic ammonia oxidizing bacteria in the biological phase X1.

[0060] Specifically, the basic threshold calculation formula is: Basic threshold = (1-X1) / X1×Z×NRR×HRT×0.05569×η.

[0061] Step S4032: Determine the biomass yield of other microorganisms based on the type of reactor.

[0062] Specifically, when the reactor is a standalone anaerobic ammonia oxidation reactor, the biomass yield of other bacteria is 0; when the reactor is a combined anaerobic ammonia oxidation reactor, the biomass yield of other bacteria is determined based on their growth.

[0063] Step S4033: Correct the basic threshold by utilizing the biomass production of other bacteria to obtain the minimum threshold for the concentration of volatile suspended solids in the influent.

[0064] Specifically, the minimum threshold for the concentration of volatile suspended solids in the influent. C VSS_in =(1-X1) / X1×Z×NRR×HRT×0.05569×η-Y_others, where Y_others represents the biomass of other bacteria.

[0065] Step S404: Determine the operating parameters for treating the wastewater using anaerobic ammonia oxidizing bacteria based on the minimum threshold of volatile suspended solids concentration in the influent.

[0066] In one optional implementation, determining the operating parameters for treating wastewater using anaerobic ammonia oxidizing bacteria based on the minimum threshold of influent volatile suspended solids concentration includes: obtaining a preset mapping matrix, which characterizes the quantitative relationship between solid-liquid separation process parameters and the corresponding effluent suspended solids concentration; and using the minimum threshold of influent volatile suspended solids concentration to search in the mapping matrix to obtain the operating parameters of the reactor pretreatment unit.

[0067] The operating parameters of the reactor pretreatment unit include at least one of the following: the dosage gradient of the chemical flocculant, the molecular weight cutoff or pore size grade of the membrane filtration unit.

[0068] The mapping matrix is ​​established based on pilot-scale experimental data. Specifically, during the design or operation phases of wastewater treatment systems based on anaerobic ammonia-oxidizing bacteria biomass balance, pilot-scale experiments are conducted according to the actual conditions of the wastewater to be treated. During the experiments, within a pre-set acceptable cost range, for wastewater with different initial suspended solids concentrations, the suspended solids concentrations in the permeate are tested or obtained from literature using different solid-liquid separation methods (such as gravity sedimentation, mechanical separation, chemical flocculation-enhanced separation, and membrane separation) under different operating parameters, thereby establishing a "technology and operating parameters - permeate suspended solids concentration" mapping matrix. This mapping matrix records the process conditions that can operate stably under acceptable cost conditions and their corresponding permeate suspended solids concentrations, where the lowest recorded value is the lowest permeate suspended solids concentration achievable under current economic and technological conditions.

[0069] Taking livestock and poultry breeding wastewater as an example, the suspended solids concentration of the effluent treated by gravity sedimentation is usually in grams per liter; after coagulation and sedimentation treatment with aluminum sulfate, the total suspended solids concentration of the effluent can be reduced to 0.3~0.6 g / L; when a combined flocculation and filtration process is used, the suspended solids concentration of the effluent is further reduced; the membrane separation process has the highest separation accuracy, and its product water suspended solids concentration can reach an even lower level (tens of milligrams per liter).

[0070] For example, the method for establishing the mapping matrix includes the following steps: Step 1: Data acquisition. Take a sample of wastewater to be treated and conduct a pretreatment experiment in a laboratory pilot device. For chemical flocculation, set a series of different flocculant dosage gradients, for example, polyaluminum chloride dosages of 20 mg / L, 50 mg / L, 100 mg / L, 200 mg / L, 500 mg / L, and 1000 mg / L; for membrane filtration, set a series of different membrane pore size levels, such as 0.1 μm, 0.5 μm, and 1 μm. Under each set condition, measure the concentration of volatile suspended solids in the treated effluent. Step 2: Mapping relationship construction. Organize the above-measured data into a two-dimensional correspondence table, with the horizontal axis representing the dosage or membrane pore size, and the vertical axis representing the corresponding effluent volatile suspended solids concentration. Based on the measured discrete data points, use a mathematical curve fitting method to obtain a continuous mathematical function that describes the quantitative relationship between the effluent volatile suspended solids concentration and the dosage or membrane pore size. The corresponding information is stored in the device's database module.

[0071] For example, the operating parameters of the reactor pretreatment unit are obtained by searching in the mapping matrix using the minimum threshold of the influent volatile suspended solids concentration. Specifically, after the system calculates the required minimum threshold of the influent volatile suspended solids concentration, the following matching operation is performed: in a pre-stored correspondence table, the minimum reagent dosage corresponding to the first occurrence of the product water volatile suspended solids concentration being less than the minimum threshold is found; or, in a mathematical function, the minimum reagent dosage that makes the product water volatile suspended solids concentration less than the minimum threshold is solved in reverse. If membrane filtration is used, the maximum permissible membrane pore size that meets the conditions is found or calculated in reverse.

[0072] Furthermore, the minimum dosage of the reagent is sent as a control command to the dosing pump, or the maximum allowable membrane pore size parameter is sent to the membrane filtration control unit, thereby adjusting the operating conditions of the pretreatment section to ensure that the actual influent volatile suspended solids concentration entering the subsequent reactor is lower than the minimum threshold.

[0073] In a further embodiment, before determining the operating parameters of the reactor pretreatment unit based on the minimum threshold of the influent volatile suspended solids concentration, the method further includes: obtaining the actual product water suspended solids concentration of the reactor; determining whether the actual product water suspended solids concentration is less than the minimum threshold of the influent volatile suspended solids concentration; and when the actual product water suspended solids concentration is greater than or equal to the minimum threshold of the influent volatile suspended solids concentration, performing the step of determining the operating parameters of the reactor pretreatment unit based on the minimum threshold of the influent volatile suspended solids concentration.

[0074] Figure 6This is a schematic diagram illustrating an example of a wastewater treatment method based on anaerobic ammonia-oxidizing bacteria biomass balance according to an embodiment of the present invention, as shown below. Figure 6 As shown, by acquiring the characteristic parameters of anaerobic ammonia oxidizing bacteria and the characteristic parameters of wastewater, a foundation is provided for the system steady-state setting in stage S2. This stage determines the target design values ​​for the reactor's nitrogen removal load (NRR), hydraulic retention time (HRT), and the proportion of anaerobic ammonia oxidizing bacteria in the biological phase (X1). Subsequently, in stage S3, the minimum threshold of influent volatile suspended solids concentration required to maintain system stability is calculated using the biomass balance formula. This threshold is used for feasibility assessment in stage S4, i.e., by comparing the minimum product effluent suspended solids concentration with the minimum influent volatile suspended solids concentration threshold, the feasibility of the scheme is verified. If the assessment is successful, the system enters the process control stage in stage S5, automatically matching and outputting optimal process parameters based on the calculation results, precisely controlling the pretreatment unit to ensure that the influent water quality meets the requirements, thereby guaranteeing the efficient and stable operation of the entire nitrogen removal system.

[0075] Figure 7 This is a schematic flow diagram of a wastewater treatment method based on anaerobic ammonia-oxidizing bacteria biomass balance according to an embodiment of the present invention, as shown below. Figure 7 As shown, the entire process begins with wastewater detection and experimental calculations. By analyzing wastewater characteristics (such as nitrogen and ammonia, total nitrite nitrogen concentration, suspended solids concentration, and COD) and anaerobic ammonia oxidizing bacteria characteristics (such as substrate consumption efficiency and growth efficiency correction factor η), a pretreatment process mapping matrix of "technical and operating parameters - suspended solids concentration in the product water" is established.

[0076] Subsequently, the wastewater enters the pretreatment unit. This unit reduces the concentration of suspended solids in the influent by selecting appropriate solid-liquid separation technology, ensuring it meets the influent requirements of the subsequent anaerobic ammonia oxidation reactor. The pretreated water then enters the core anaerobic ammonia oxidation reactor, where nitrogenous pollutants are efficiently removed under set design parameters. Finally, the treated wastewater meets discharge standards, completing the entire treatment process.

[0077] In summary, the wastewater treatment method based on anaerobic ammonia-oxidizing bacteria biomass balance provided in this embodiment has the following beneficial effects: First, it breaks through the limitations of traditional biochemical inhibition theory. For the first time, it reveals from the perspective of physical constraints that the essence of the collapse of anaerobic ammonia oxidation systems in complex wastewater treatment is the imbalance of biomass balance, providing new theoretical support for the treatment of wastewater with high suspended solids.

[0078] Secondly, it significantly improves the accuracy of design under complex operating conditions. By introducing a characteristic correction factor η for pig farm wastewater, it corrects the blind optimism about biomass growth in traditional design, making the system design boundary more consistent with the actual engineering operating environment.

[0079] Third, it enables early warning and dynamic compensation for system stability. Using the influent suspended solids concentration threshold as the core criterion, it can keenly detect minute deviations before the system experiences physical collapse. By adjusting the carrier characteristics or sludge replenishment, the system possesses extremely strong shock resistance and self-repair capabilities.

[0080] Fourth, it balances efficient nitrogen removal with long-term stable operation. This method does not rely on expensive additives or complex extreme control conditions; it can be achieved by optimizing pretreatment and physical retention methods. It features simple operation, low cost, high repeatability, and ease of promotion and application in large-scale pig farm wastewater treatment projects.

[0081] To illustrate the wastewater treatment method based on anaerobic ammonia oxidizing bacteria biomass balance in this embodiment more clearly, several specific examples are given.

[0082] Example 1: Growth efficiency correction factor η = (Net growth of anaerobic ammonia oxidizing bacteria + Effluent loss of anaerobic ammonia oxidizing bacteria) / Theoretical growth of anaerobic ammonia oxidizing bacteria = 0.5. Figure 8 The growth of anaerobic ammonia-oxidizing bacteria was shown in the water distribution stage (influent suspended solids concentration = 0) and the actual aquaculture wastewater stage (influent suspended solids concentration = 0.05 g V suspended solids concentration / L). Figure 9 The variation of the proportion (X2) of anammox bacteria in the biological phase in a 1L laboratory-scale anammox reactor is shown. The theoretical growth rate of anammox bacteria is 0.05569 g / g N. With actual aquaculture wastewater as the influent, the hydraulic retention time (HRT) is 3.8 days. The non-return flow rate (NRR) is 0.13 g N / L / day. The system biomass MLVSS is approximately 3.0 g VSS / L, and the maximum substrate consumption rate of anammox bacteria is 0.32 g N / g AnAOB / day. Under these conditions, based on the second constraint, the minimum design value (X1) of the anammox bacteria proportion is calculated to be 12.75%.

[0083] Calculate C VSS_in =(1-X1) / X1×Z×NRR×HRT×0.05569×η=0.09 g VSS / L.

[0084] Meets the actual influent SS (0.05 g VSS / L) requirement. <C VSS_in (0.09 g VSS / L), therefore the biomass of anaerobic ammonia oxidizing bacteria in the whole system remained stable, and the actual measured proportion of anaerobic ammonia oxidizing bacteria X2 was 20%, which was also higher than the preset X1 value of 13%.

[0085] Example 2: In a pilot-scale reactor (effective volume 3.3 m³) 3In the study, under different stages of influent (S1 and S4, influent SS=0) and actual aquaculture wastewater (S3 (influent SS=1.67 g VSS / L) and S4 (influent SS=0.61 g VSS / L)), SS and BS represent suspended sludge and biofilm sludge, respectively. The percentage of anaerobic ammonia-oxidizing bacteria in the biological phase, determined by 16S amplicon sequencing technology, is shown multiplied by 2. Figure 10 As shown in the figure, the operational data from stages S1 and S4 indicate that the higher the influent suspended solids (SS) concentration, the faster the rate of decline in the proportion of anaerobic ammonia oxidizing bacteria in the biological phase; and both suspended and biofilm-covered bacteria show a continuous downward trend in their proportion. These results suggest that while biofilm-covered sludge (i.e., the loading medium) can slow down the loss of anaerobic ammonia oxidizing bacteria to some extent, it cannot fundamentally prevent system collapse under long-term operating conditions.

[0086] Example 3: In the pilot-scale reactor, the influent for stages S1 and S4 was pre-mixed water (influent SS=0), while the influent for stages S3 and S4 was actual aquaculture wastewater (S3 (influent SS=1.67 g VSS / L) and S4 (influent SS=0.61 g VSS / L)). SS and BS represent suspended sludge and biofilm sludge, respectively. In the laboratory reactor, the influent SS for the pre-mixed water stage was 0; the influent SS for the actual aquaculture wastewater stage was 0.05 g VSS / L. The net growth of anaerobic ammonia oxidizing bacteria differed based on different influent types and SS levels, as shown below. Figure 11 As shown. When the SS in the influent is higher than C... VSS_in In stages S3 and S4, when the influent SS was 0.09 g VSS / L, a significant loss of anaerobic ammonia oxidizing bacteria was observed, indicating insufficient long-term operational stability of the system. When the influent SS was below this minimum threshold (such as in stages S1, S4, and the laboratory reactor operation), the abundance of anaerobic ammonia oxidizing bacteria was maintained or even significantly increased, further demonstrating that controlling the influent SS below this threshold is a key condition for maintaining stable system operation.

[0087] This embodiment also provides a wastewater treatment device based on anaerobic ammonia-oxidizing bacteria biomass balance. This device is used to implement the above embodiments and preferred embodiments, and details already described will not be repeated. As used below, the term "module" can refer to a combination of software and / or hardware that performs a predetermined function. Although the device described in the following embodiments is preferably implemented in software, hardware implementation, or a combination of software and hardware, is also possible and contemplated.

[0088] like Figure 12 As shown, the present invention also provides a wastewater treatment device based on the biomass balance of anaerobic ammonia-oxidizing bacteria, comprising: The first acquisition module 1201 is used to acquire the growth efficiency correction factor η of anaerobic ammonia oxidizing bacteria; The second acquisition module 1202 is used to acquire the target design value of denitrification load NRR, the target design value of hydraulic retention time HRT, and the target design value of the proportion of anaerobic ammonia oxidizing bacteria in the biological phase X1 of the reactor. Calculation module 1203 is used to calculate the minimum threshold of influent volatile suspended solids concentration of the wastewater to be treated based on the growth efficiency correction factor η, the target design value of denitrification load NRR, the target design value of hydraulic retention time HRT, and the target design value of the proportion of anaerobic ammonia oxidizing bacteria in the biological phase X1. The operating parameter determination module 1204 is used to determine the operating parameters of the reactor pretreatment unit based on the minimum threshold of the volatile suspended solids concentration in the influent.

[0089] In some optional implementations, the second acquisition module 1202 is specifically used to: acquire the influent nitrogen concentration C in the wastewater to be treated. N ; Obtain the nitrogen removal percentage Z from the anaerobic ammonia oxidation pathway; Based on the first constraint, according to the influent nitrogen concentration C N The proportion of nitrogen removal via the anaerobic ammonia oxidation pathway, Z, was used to screen the initial values ​​of the denitrification load and hydraulic retention time to obtain a data set that met the first constraint condition. This data set included the initial design values ​​of the denitrification load and hydraulic retention time. The substrate consumption efficiency q of the anaerobic ammonia oxidizing bacteria was then obtained. s ; Obtain the suspended sludge concentration (MLVSS) in the reactor and the percentage (X2) of anaerobic ammonia-oxidizing bacteria in the biological phase of the wastewater to be treated; Based on the second constraint, utilize the substrate consumption efficiency q s The initial design value of denitrification load was screened by measuring the suspended sludge concentration (MLVSS) and the proportion of anaerobic ammonia oxidizing bacteria in the biological phase of the wastewater to be treated (X2). The target design value of denitrification load (NRR) and the target design value of the proportion of anaerobic ammonia oxidizing bacteria in the biological phase (X1) were determined. The initial design value of hydraulic retention time (HRT) paired with the target design value of denitrification load (NRR) in the data set was extracted and determined as the target design value of hydraulic retention time (HRT).

[0090] In some optional implementations, the calculation module 1203 is specifically used to: calculate the basic threshold using a preset basic threshold calculation formula based on the growth efficiency correction factor η, the target design value of denitrification load NRR, the target design value of hydraulic retention time HRT, and the target design value of the proportion of anaerobic ammonia oxidizing bacteria in the biological phase X1; determine the biomass yield of other bacteria according to the type of reactor; and correct the basic threshold using the biomass yield of other bacteria to obtain the minimum threshold for the concentration of volatile suspended solids in the influent.

[0091] In some optional embodiments, the wastewater treatment device based on anaerobic ammonia oxidizing bacteria biomass balance further includes a correction module. After calculating the minimum threshold for the influent volatile suspended solids concentration of the wastewater to be treated based on the growth efficiency correction factor η, the target design value of denitrification load NRR, the target design value of hydraulic retention time HRT, and the target design value of the proportion of anaerobic ammonia oxidizing bacteria in the biological phase X1, the correction module is used to: obtain the minimum product volatile suspended solids concentration of the reactor; determine whether the minimum threshold for the influent volatile suspended solids concentration is greater than the minimum product volatile suspended solids concentration; when the minimum threshold for the influent volatile suspended solids concentration is less than or equal to the minimum product volatile suspended solids concentration, after adjusting the suspended sludge concentration MLVSS of the reactor, recalculate the minimum threshold for the influent volatile suspended solids concentration.

[0092] In some optional implementations, the operating parameter determination module 1204 is specifically used to: obtain a preset mapping matrix, which characterizes the quantitative relationship between process parameters and the corresponding effluent suspended solids concentration; and use the minimum threshold of influent volatile suspended solids concentration to search in the mapping matrix to obtain the operating parameters of the reactor pretreatment unit.

[0093] In some optional embodiments, before determining the operating parameters of the reactor pretreatment unit based on the minimum threshold of the influent volatile suspended solids concentration, the operating parameter determination module 1204 is specifically used to: obtain the actual product water suspended solids concentration of the reactor; determine whether the actual product water suspended solids concentration is less than the minimum threshold of the influent volatile suspended solids concentration; and when the actual product water suspended solids concentration is greater than or equal to the minimum threshold of the influent volatile suspended solids concentration, perform the step of determining the operating parameters of the reactor pretreatment unit based on the minimum threshold of the influent volatile suspended solids concentration.

[0094] The wastewater treatment device based on anaerobic ammonia oxidizing bacteria biomass balance provided in this embodiment of the invention can execute the wastewater treatment method based on anaerobic ammonia oxidizing bacteria biomass balance provided in any embodiment of the invention, and has the corresponding functional modules and beneficial effects for executing the method. Further functional descriptions of the above modules and units are the same as in the corresponding embodiments described above, and will not be repeated here.

[0095] Figure 13 This is a schematic diagram of the structure of an electronic device provided in an embodiment of the present invention.

[0096] The following is a detailed reference. Figure 13This diagram illustrates a suitable structural schematic for implementing an electronic device according to embodiments of the present invention. The electronic device may include a processor (e.g., a central processing unit, graphics processor, etc.) 1301, which can perform various appropriate actions and processes according to a program stored in read-only memory (ROM) 1302 or a program loaded from memory 1308 into random access memory (RAM) 1303. The RAM 1303 also stores various programs and data required for the operation of the electronic device. The processor 1301, ROM 1302, and RAM 1303 are interconnected via a bus 1304. An input / output (I / O) interface 1305 is also connected to the bus 1304.

[0097] Typically, the following devices can be connected to I / O interface 1305: input devices 1306 including, for example, touchscreens, touchpads, keyboards, mice, cameras, microphones, accelerometers, gyroscopes, etc.; output devices 1307 including, for example, liquid crystal displays (LCDs), speakers, vibrators, etc.; memory devices 1308 including, for example, magnetic tapes, hard disks, etc.; and communication devices 1309. Communication device 1309 allows electronic devices to communicate wirelessly or wiredly with other devices to exchange data. Although Figure 13 Electronic devices with various devices are shown, but it should be understood that it is not required to implement or have all of the devices shown, and more or fewer devices may be implemented or have instead.

[0098] In particular, according to embodiments of the present invention, the processes described above with reference to the flowcharts can be implemented as computer software programs. For example, embodiments of the present invention include a computer program product comprising a computer program carried on a non-transitory computer-readable medium, the computer program containing program code for performing the methods shown in the flowcharts. In such embodiments, the computer program can be downloaded and installed from a network via a communication device 1309, or installed from a memory 1308, or installed from a ROM 1302. When the computer program is executed by the processor 1301, it performs the functions defined in the wastewater treatment method based on anaerobic ammonia-oxidizing bacteria biomass balance according to embodiments of the present invention.

[0099] Figure 13 The electronic device shown is merely an example and should not be construed as limiting the functionality and scope of use of the embodiments of the present invention.

[0100] This invention also provides a computer-readable storage medium. The methods described above according to embodiments of the invention can be implemented in hardware or firmware, or implemented as computer code that can be recorded on a storage medium, or implemented as computer code downloaded via a network and originally stored on a remote storage medium or a non-transitory machine-readable storage medium and then stored on a local storage medium. Thus, the methods described herein can be processed by software stored on a storage medium using a general-purpose computer, a dedicated processor, or programmable or dedicated hardware. The storage medium can be a magnetic disk, optical disk, read-only memory, random access memory, flash memory, hard disk, or solid-state drive, etc.; further, the storage medium can also include combinations of the above types of memory. It is understood that computers, processors, microprocessor controllers, or programmable hardware include storage components capable of storing or receiving software or computer code. When the software or computer code is accessed and executed by the computer, processor, or hardware, the wastewater treatment method based on anaerobic ammonia-oxidizing bacteria biomass balance shown in the above embodiments is implemented.

[0101] A portion of this invention can be applied as a computer program product, such as computer program instructions, which, when executed by a computer, can invoke or provide the methods and / or technical solutions according to the invention through the operation of the computer. Those skilled in the art will understand that the forms in which computer program instructions exist in a computer-readable medium include, but are not limited to, source files, executable files, installation package files, etc. Correspondingly, the ways in which computer program instructions are executed by a computer include, but are not limited to: the computer directly executing the instructions, or the computer compiling the instructions and then executing the corresponding compiled program, or the computer reading and executing the instructions, or the computer reading and installing the instructions and then executing the corresponding installed program. Here, the computer-readable medium can be any available computer-readable storage medium or communication medium accessible to a computer.

[0102] Although embodiments of the invention have been described in conjunction with the accompanying drawings, those skilled in the art can make various modifications and variations without departing from the spirit and scope of the invention, and such modifications and variations all fall within the scope defined by the appended claims.

Claims

1. A wastewater treatment method based on anaerobic ammonia-oxidizing bacteria biomass balance, characterized in that, The method includes: Obtain the growth efficiency correction factor for anaerobic ammonia oxidizing bacteria; Obtain the target design values ​​for the denitrification load, hydraulic retention time, and the proportion of anaerobic ammonia-oxidizing bacteria in the biological phase of the reactor; The minimum threshold for the concentration of volatile suspended solids in the influent of the wastewater to be treated is calculated based on the growth efficiency correction factor, the target design value of denitrification load, the target design value of hydraulic retention time, and the target design value of the proportion of anaerobic ammonia oxidizing bacteria in the biological phase. The operating parameters of the reactor pretreatment unit are determined based on the minimum threshold of the influent volatile suspended solids concentration.

2. The method according to claim 1, characterized in that, The target design values ​​for the denitrification load, hydraulic retention time, and proportion of anaerobic ammonia-oxidizing bacteria in the biological phase of the reactor are obtained as follows: Obtain the influent nitrogen concentration in the wastewater to be treated; Obtain the proportion of nitrogen removal via the anaerobic ammonium oxidation pathway; Based on the first constraint, according to the influent nitrogen concentration and the nitrogen removal ratio Z of the anaerobic ammonia oxidation pathway, the initial value of the denitrification load and the initial value of the hydraulic retention time are screened to obtain a data set that meets the first constraint, wherein the data set includes the initial design value of the denitrification load and the initial design value of the hydraulic retention time; Obtain the substrate consumption efficiency of the anaerobic ammonia-oxidizing bacteria; The concentration of suspended sludge in the reactor and the proportion of anaerobic ammonia-oxidizing bacteria in the biological phase of the wastewater to be treated were obtained. Based on the second constraint, the initial design value of the denitrification load is screened using the substrate consumption efficiency, the suspended sludge concentration, and the proportion of anaerobic ammonia oxidizing bacteria in the biological phase of the wastewater to be treated, so as to determine the target design value of the denitrification load and the target design value of the proportion of anaerobic ammonia oxidizing bacteria in the biological phase. Extract the initial design value of hydraulic residence time from the data set that is paired with the target design value of the denitrification load, and determine it as the target design value of hydraulic residence time.

3. The method according to claim 1, characterized in that, The minimum threshold for influent volatile suspended solids concentration in the wastewater to be treated, calculated based on the growth efficiency correction factor, the target design value for denitrification load, the target design value for hydraulic retention time, and the target design value for the proportion of anaerobic ammonia-oxidizing bacteria in the biological phase, includes: The basic threshold is calculated using a preset basic threshold calculation formula based on the growth efficiency correction factor, the target design value of denitrification load, the target design value of hydraulic retention time, and the target design value of the proportion of anaerobic ammonia oxidizing bacteria in the biological phase. The biomass yield of other microorganisms is determined based on the type of reactor. The baseline threshold is corrected using the biomass production of the other bacteria to obtain the minimum threshold for the concentration of volatile suspended solids in the influent.

4. The method according to claim 1, characterized in that, After calculating the minimum threshold for the influent volatile suspended solids concentration of the wastewater to be treated based on the growth efficiency correction factor, the target design value for denitrification load, the target design value for hydraulic retention time, and the target design value for the proportion of anaerobic ammonia-oxidizing bacteria in the biological phase, the following steps are also included: Obtain the lowest concentration of suspended solids in the pretreatment water of the reactor; Determine whether the minimum threshold for the concentration of volatile suspended solids in the influent is greater than the minimum concentration of suspended solids in the product water; When the minimum threshold for the concentration of volatile suspended solids in the influent is less than or equal to the minimum concentration of suspended solids in the permeate, the minimum threshold for the concentration of volatile suspended solids in the influent is recalculated after adjusting the concentration of suspended sludge in the reactor.

5. The method according to claim 1, characterized in that, The operating parameters for treating the wastewater using the anaerobic ammonia-oxidizing bacteria, determined based on the minimum threshold of the influent volatile suspended solids concentration, include: A preset mapping matrix is ​​obtained, which represents the quantitative relationship between solid-liquid separation process parameters and the corresponding effluent suspended solids concentration; the minimum threshold of influent volatile suspended solids concentration is used to search in the mapping matrix to obtain the operating parameters of the reactor pretreatment unit.

6. The method according to claim 1, characterized in that, Before determining the operating parameters of the reactor pretreatment unit based on the minimum threshold of the influent volatile suspended solids concentration, the method further includes: Obtain the actual suspended solids concentration in the product water of the reactor; Determine whether the actual concentration of suspended solids in the produced water is less than the minimum threshold for the concentration of volatile suspended solids in the influent; When the actual product water suspended solids concentration is greater than or equal to the minimum threshold of the influent volatile suspended solids concentration, the step of determining the operating parameters of the reactor pretreatment unit based on the minimum threshold of the influent volatile suspended solids concentration is performed.

7. A wastewater treatment device based on anaerobic ammonia-oxidizing bacteria biomass balance, characterized in that, The device includes: The first acquisition module is used to acquire the growth efficiency correction factor of anaerobic ammonia oxidizing bacteria; The second acquisition module is used to acquire the target design value of the denitrification load, the target design value of the hydraulic retention time (HRT), and the target design value of the proportion of anaerobic ammonia oxidizing bacteria in the biological phase of the reactor. The calculation module is used to calculate the minimum threshold of influent volatile suspended solids concentration in the wastewater to be treated based on the growth efficiency correction factor, the target design value of denitrification load, the target design value of hydraulic retention time, and the target design value of the proportion of anaerobic ammonia oxidizing bacteria in the biological phase. The operating parameter determination module is used to determine the operating parameters of the reactor pretreatment unit based on the minimum threshold of the influent volatile suspended solids concentration.

8. An electronic device, characterized in that, include: The system includes a memory and a processor, which are interconnected. The memory stores computer instructions, and the processor executes the computer instructions to perform the wastewater treatment method based on the biomass balance of anaerobic ammonia-oxidizing bacteria as described in any one of claims 1-6.

9. A computer-readable storage medium, characterized in that, The computer-readable storage medium stores computer instructions for causing the computer to perform the wastewater treatment method based on the biomass balance of anaerobic ammonia oxidizing bacteria as described in any one of claims 1-6.

10. A computer program product, characterized in that, Includes computer instructions for causing a computer to perform the wastewater treatment method based on the biomass balance of anaerobic ammonia oxidizing bacteria as described in any one of claims 1-6.

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