A synergistic bioremediation process for purifying a contaminated water body

Abstract

The present application relates to the field of water pollution control and treatment technology, and discloses a kind of contaminated water purification's synergistic bioremediation process, comprising: collecting the real-time oxidation-reduction potential of water to be treated and real-time water temperature, using real-time water temperature to compensate potential decay rate to establish metabolic intensity reference value, calculate potential time sequence second-order change rate to identify electron transfer acceleration characteristics, monitor change rate negative peak, and when the deviation of negative peak and metabolic intensity reference value exceeds threshold, start time sequence non-uniform pulsed microbubble aeration, synchronously add electron acceptor, the present application uses the potential gradient formed in aeration moment to drive special degrading bacterial group to directional oxidation of metabolic product formed in acid production stage, selectively inhibit indigenous heterotrophic bacterial group proliferation by potential time sequence rebound, effectively guarantee the colonization advantage and succession stability of remediation bacterial group in open environment.

Description

Technical Field

[0001] This invention relates to a synergistic bioremediation process for purifying polluted water bodies, belonging to the field of water pollution control and treatment technology. Background Technology

[0002] Current co-bioremediation processes for polluted water bodies utilize microbial metabolic activities to degrade pollutants. This is achieved by adding compound microbial agents to the target water body, along with continuous aeration and periodic nutrient replenishment, to maintain the apparent metabolic activity of the aquatic ecosystem. This approach relies on constructing a relatively stable dissolved oxygen gradient and nutrient load environment to maximize the apparent efficiency of pollutant degradation. However, in open remediation systems such as natural water bodies, this steady-state environment construction strategy generates significant negative effects of community competition. Indigenous heterotrophic microbial communities typically have shorter doubling cycles and stronger capture capabilities for general substrates. A continuous and stable substrate supply and dissolved oxygen transport pattern favors indigenous microbial communities occupying dominant ecological niches. As the remediation process progresses, indigenous microbial communities, through spatial hindrance and nutrient monopoly effects, limit the colonization space of exogenous engineered microbial communities, leading to a shortened effective survival period for bacteria that degrade specific pollutants, thereby reducing the long-term operational stability of the remediation system.

[0003] Besides limitations in hardware layout and bioremediation system construction, existing technologies also have shortcomings in precise feedback and dynamic control of biochemical processes. For example, Chinese invention patent application CN102874934A discloses a technology for direct in-situ treatment, purification, and ecological restoration of polluted water bodies. This technology creates forced vertical convection by using a water flow stirring and lifting machine, and combines biofilm packing materials with aquatic plants and animals to construct an ecological restoration system. This technical approach belongs to a steady-state restoration mode based on physical reinforcement and static biological carriers. Although the continuous weak circulation created enhances surface reoxygenation, it also leads to the water body being under a homogenized physicochemical gradient for a long time, lacking deep intervention in the rhythm of biochemical reactions within the water body. In actual open working conditions, the environment is more likely to stimulate the exponential proliferation of native dominant heterotrophic bacteria, making it impossible to open an independent succession window for special degradation bacteria on the time axis. This scheme lacks the extraction of the characteristics of microbial metabolic stage transitions, making it difficult to cope with the dynamic impact of pollution load and environmental temperature fluctuations in natural water bodies, resulting in a mismatch between substrate addition and biological needs in time and space.

[0004] Therefore, the technical problem to be solved by this invention is how to reconstruct the succession sequence of microbial communities based on the biochemical feedback mechanism of water bodies, break the steady-state monopoly of indigenous microbial communities on remediation resources, and establish the temporal home field advantage of special degradation pathways. Summary of the Invention

[0005] To address the problems mentioned in the background art, the technical solution of the present invention is as follows: A synergistic bioremediation process for purifying polluted water bodies, comprising the following steps:

[0006] Step S1: Obtain real-time oxidation-reduction potential data and real-time water temperature data of the water body to be treated;

[0007] Step S2: Use real-time water temperature data to perform kinetic compensation on the preset room temperature potential decay rate, and establish a potential decay benchmark value that characterizes the metabolic intensity of the microbial community inside the water body to be treated. The compensation process corrects the nonlinear sensitivity of the biochemical reaction rate to temperature fluctuations through the Arrhenius kinetic equation.

[0008] Step S3: Calculate the time-series second-order rate of change of real-time redox potential with sampling time to identify the acceleration characteristics of the electron transport chain in water at the metabolic peak point.

[0009] Step S4: Monitor the second-order change rate over time. When it shows a negative peak and the deviation of the negative peak from the potential decay reference value exceeds the preset metabolic extreme value alarm threshold, turn on the non-uniform pulsed microbubble aeration to the water body to be treated to interrupt the original anaerobic fermentation steady state environment.

[0010] Step S5: During the aeration cycle of time-dissipative pulsed microbubble aeration, an electron acceptor is simultaneously introduced into the water to be treated. The dramatic gradient jump in redox potential generated at the interface between the water and sediment during aeration drives the special degrading bacteria to target and oxidize the intermediate metabolites accumulated in the previous acid production stage. Through the nonlinear recovery of redox potential over time, the exponential proliferation of the native dominant heterotrophic bacteria is selectively inhibited, thereby ensuring the colonization density and succession advantage of the special degrading bacteria in the open water environment.

[0011] Preferably, the process of obtaining the potential decay benchmark value in step S2 includes: step S21, calculating the real-time metabolic correction factor based on the real-time water temperature and the preset Arrhenius correction coefficient; step S22, the real-time metabolic correction factor is positively correlated with the real-time water temperature, and by adjusting the temperature sensitivity of the biochemical reaction rate, the benchmark decay slope under 20℃ condition is converted into a potential decay benchmark value that matches the current operating conditions, so that the negative peak determination criterion in step S4 has seasonal adaptability.

[0012] Preferably, the parameters for the time-sequential non-uniform pulsed microbubble aeration in step S4 are limited to: microbubble diameter of 10 mm. m to 50 m, the time ratio of the anaerobic phase to the aerobic phase in a single aeration pulse cycle is set to 3:1 to 5:1; by maintaining a long-cycle reducing environment, special degrading bacteria are induced to secrete oxygenases targeting recalcitrant organic matter, and short-cycle strong oxidation pulses are used to complete substrate mineralization.

[0013] Preferably, the process of adding electron acceptor in step S5 includes: obtaining the real-time redox potential at the potential recovery rate after the start of sequential non-uniform pulsed microbubble aeration; when the potential recovery rate is lower than the preset 5mV / h, linearly increasing the instantaneous concentration of electron acceptor until the potential recovery rate recovers to above 5mV / h, so as to eliminate the mass transfer resistance at the sediment interface.

[0014] Preferably, the method further includes a sensor calibration step: Step S6, obtaining the probe micro-differential value of the potential probe that collects real-time redox potential data; Step S7, using the potential transient response characteristic curve induced by carbon source pulse injection, combined with the probe micro-differential value, to complete in-situ drift compensation of the potential probe, so as to eliminate the systematic deviation caused by the biofilm adhesion on the surface of the potential probe on the redox potential measurement accuracy.

[0015] Preferably, the timing control rules for non-uniform pulsed microbubble aeration include: monitoring the highest potential value at the end of the aerobic phase; when the highest potential value shows a monotonically decreasing trend within three consecutive aeration pulse cycles, automatically shortening the duration of the anaerobic phase in subsequent pulse cycles, and simultaneously increasing the frequency of electron acceptor delivery to prevent excessive acidification of the water.

[0016] Preferably, in step S5, the physical shear force generated by time-sequential non-uniform pulsed microbubble aeration is used to break up the bacterial floc structure formed by the indigenous dominant heterotrophic bacteria in the water to be treated; by peeling off the indigenous dominant heterotrophic bacteria, the active attachment sites on the surface of the bottom sediment of the water to be treated are exposed, providing physical space for the amplification of special degrading bacteria.

[0017] Preferably, the electron acceptor is perchlorate, nitrate, or hydrogen peroxide; the concentration of the electron acceptor is matched with the concentration gradient based on the real-time monitoring value of the total organic carbon in the water to be treated, and the electron acceptor release is controlled at the moment when the negative extreme value of the second-order rate of change occurs, so as to realize the dynamic coupling between chemical agent addition and microbial metabolic rhythm.

[0018] Preferably, after step S5, the method further includes: acquiring real-time transparency data of the water body to be treated; when the real-time transparency data reaches 50cm or more, reducing the output power of the time-series non-uniform pulsed microbubble aeration, and utilizing the oxygen secretion effect of aquatic plant roots to maintain the steady state of the redox potential of the water body to be treated under low oxygen load.

[0019] Compared with the prior art, the beneficial effects of the present invention are:

[0020] 1. In the synergistic bioremediation of polluted water bodies, by calculating the first derivative of the redox potential of the polluted water body and combining it with the potential decay reference rate based on real-time water temperature correction, the biochemical state of primary electron acceptor depletion in the water body can be accurately captured. This sensing mechanism breaks the inertia of traditional bioremediation processes that rely on steady-state oxygen supply and continuous feeding. After determining that the electron acceptor is depleted, it actively interrupts the oxygen supply and switches to a high-concentration carbon source pulse. This asymmetric temporal regulation forcibly separates the resource utilization period of aerobic competitive bacteria and facultative anaerobic engineered bacteria on the time axis, effectively solving the spatial steric hindrance and nutrient suppression problems caused by continuous substrate supply to indigenous heterotrophic bacteria, thereby ensuring the population advantage and colonization rate of special degradation bacteria in complex open water bodies.

[0021] 2. By using the negative inflection point of the second derivative of the oxidation-reduction potential as the trigger signal for the microbubble aeration pulse, the peak value of the acid production process in the anaerobic fermentation stage is precisely targeted. Through this triggering mechanism based on the bottom metabolic feedback, the process enters strong aeration at the transient point where the accumulation of metabolic intermediates is the largest. The rapidly rising potential gradient drives the aerobic oxidation process. This design transforms the mass transfer barrier that was originally difficult to overcome in physical space into an orderly metabolic relay on the time axis, allowing easily degradable small molecules generated by anaerobic hydrolysis to quickly enter the aerobic degradation pathway, thereby improving the characteristic degradation rate of recalcitrant organic matter in polluted water bodies.

[0022] 3. By introducing an environmental temperature correction coefficient and the Arrhenius kinetic equation to establish a potential decay benchmark, the biochemical activity of polluted water bodies is significantly affected by seasonal temperature fluctuations. Traditional control strategies with fixed durations or static thresholds are prone to causing misalignment between process switching points and actual microbial metabolic stages. This invention uses a temperature compensation mechanism to automatically match process judgment parameters with the real-time metabolic kinetic characteristics of the water body. Without relying on complex biological monitoring sensors, it ensures the consistency of the biochemical response of the purification process under different temperature conditions, enhancing the universality of the solution in natural water body restoration projects. Attached Figure Description

[0023] Figure 1 This is a flowchart illustrating the synergistic bioremediation process based on metabolic feedback of the present invention.

[0024] Figure 2 This is a system architecture diagram illustrating the core mechanism and multi-dimensional control logic of the process of this invention.

[0025] The objectives, features, and advantages of this invention will be further explained in conjunction with the embodiments and with reference to the accompanying drawings. Detailed Implementation

[0026] The technical solutions of the embodiments of this application will be clearly described below with reference to the accompanying drawings. Obviously, the described embodiments are only some embodiments of this application, not all embodiments. All other embodiments obtained by those skilled in the art based on the embodiments of this application are within the scope of protection of this application.

[0027] A synergistic bioremediation process for purifying contaminated water includes the following steps:

[0028] Step S1: Obtain real-time oxidation-reduction potential data and real-time water temperature data of the water body to be treated;

[0029] Step S2: Use real-time water temperature data to perform kinetic compensation on the preset room temperature potential decay rate, and establish a potential decay benchmark value that characterizes the metabolic intensity of the microbial community inside the water body to be treated. The compensation process corrects the nonlinear sensitivity of the biochemical reaction rate to temperature fluctuations through the Arrhenius kinetic equation.

[0030] Step S3: Calculate the time-series second-order rate of change of real-time redox potential with sampling time to identify the acceleration characteristics of the electron transport chain in water at the metabolic peak point.

[0031] Step S4: Monitor the second-order change rate over time. When it shows a negative peak and the deviation of the negative peak from the potential decay reference value exceeds the preset metabolic extreme value alarm threshold, turn on the non-uniform pulsed microbubble aeration to the water body to be treated to interrupt the original anaerobic fermentation steady state environment.

[0032] Step S5: During the aeration cycle of time-dissipative pulsed microbubble aeration, an electron acceptor is simultaneously introduced into the water to be treated. The dramatic gradient jump in redox potential generated at the interface between the water and sediment during aeration drives the special degrading bacteria to target and oxidize the intermediate metabolites accumulated in the previous acid production stage. Through the nonlinear recovery of redox potential over time, the exponential proliferation of the native dominant heterotrophic bacteria is selectively inhibited, thereby ensuring the colonization density and succession advantage of the special degrading bacteria in the open water environment.

[0033] Preferably, the process of obtaining the potential decay benchmark value in step S2 includes: step S21, calculating the real-time metabolic correction factor based on the real-time water temperature and the preset Arrhenius correction coefficient; step S22, the real-time metabolic correction factor is positively correlated with the real-time water temperature, and by adjusting the temperature sensitivity of the biochemical reaction rate, the benchmark decay slope under 20℃ condition is converted into a potential decay benchmark value that matches the current operating conditions, so that the negative peak determination criterion in step S4 has seasonal adaptability.

[0034] Preferably, the parameters for the time-sequential non-uniform pulsed microbubble aeration in step S4 are limited to: microbubble diameter of 10 mm. m to 50 m, the time ratio of the anaerobic phase to the aerobic phase in a single aeration pulse cycle is set to 3:1 to 5:1; by maintaining a long-cycle reducing environment, special degrading bacteria are induced to secrete oxygenases targeting recalcitrant organic matter, and short-cycle strong oxidation pulses are used to complete substrate mineralization.

[0035] Preferably, the process of adding electron acceptor in step S5 includes: obtaining the real-time redox potential at the potential recovery rate after the start of sequential non-uniform pulsed microbubble aeration; when the potential recovery rate is lower than the preset 5mV / h, linearly increasing the instantaneous concentration of electron acceptor until the potential recovery rate recovers to above 5mV / h, so as to eliminate the mass transfer resistance at the sediment interface.

[0036] Preferably, the method further includes a sensor calibration step: Step S6, obtaining the probe micro-differential value of the potential probe that collects real-time redox potential data; Step S7, using the potential transient response characteristic curve induced by carbon source pulse injection, combined with the probe micro-differential value, to complete in-situ drift compensation of the potential probe, so as to eliminate the systematic deviation caused by the biofilm adhesion on the surface of the potential probe on the redox potential measurement accuracy.

[0037] Preferably, the timing control rules for non-uniform pulsed microbubble aeration include: monitoring the highest potential value at the end of the aerobic phase; when the highest potential value shows a monotonically decreasing trend within three consecutive aeration pulse cycles, automatically shortening the duration of the anaerobic phase in subsequent pulse cycles, and simultaneously increasing the frequency of electron acceptor delivery to prevent excessive acidification of the water.

[0038] Preferably, in step S5, the physical shear force generated by time-sequential non-uniform pulsed microbubble aeration is used to break up the bacterial floc structure formed by the indigenous dominant heterotrophic bacteria in the water to be treated; by peeling off the indigenous dominant heterotrophic bacteria, the active attachment sites on the surface of the bottom sediment of the water to be treated are exposed, providing physical space for the amplification of special degrading bacteria.

[0039] Preferably, the electron acceptor is perchlorate, nitrate, or hydrogen peroxide; the concentration of the electron acceptor is matched with the concentration gradient based on the real-time monitoring value of the total organic carbon in the water to be treated, and the electron acceptor release is controlled at the moment when the negative extreme value of the second-order rate of change occurs, so as to realize the dynamic coupling between chemical agent addition and microbial metabolic rhythm.

[0040] Preferably, after step S5, the method further includes: acquiring real-time transparency data of the water body to be treated; when the real-time transparency data reaches 50cm or more, reducing the output power of the time-series non-uniform pulsed microbubble aeration, and utilizing the oxygen secretion effect of aquatic plant roots to maintain the steady state of the redox potential of the water body to be treated under low oxygen load.

[0041] Example 1: In the scenario of remediation of the interface between sediment and water in a large shallow lake that has suffered from long-term combined pollution from industrial wastewater and agricultural non-point source pollution, the water to be treated has been in a state of stratified eutrophication for a long time and the ambient temperature fluctuates drastically with the seasons. Traditional synergistic bioremediation methods use continuous aeration to maintain dissolved oxygen concentration and periodically add nutrients. The continuous and stable physicochemical gradient environment screens and solidifies native dominant heterotrophic bacteria with short growth cycles and high affinity for conventional substrates. As a result, the artificially added special degrading bacteria are at a disadvantage in competing for electron acceptors. Due to the competitive exclusion effect, the population declines and mass transfer is restricted at the sediment interface, exposing the contradiction between the steady-state nutrient supply mechanism and the long-term colonization requirements of special microorganisms.

[0042] A sensor array deployed in the treatment area continuously acquires real-time oxidation-reduction potential (ORP) and water temperature data of the water to be treated at a sampling period of 10 seconds. After receiving this data, the control unit extracts a preset Arrhenius correction coefficient and uses real-time water temperature data to perform kinetic compensation on a preset ambient temperature potential decay rate. The nonlinear sensitivity of the biochemical reaction rate to temperature fluctuations is corrected using the Arrhenius kinetic equation, establishing a potential decay benchmark value characterizing the metabolic intensity of the microbial community within the water body. Kinetic compensation eliminates parameter misjudgments caused by physical solubility and slow biochemical reactions during cold water periods. Based on this, the control unit continuously calculates the temporal second-order rate of change of real-time ORP with sampling time to identify the acceleration characteristics of the water body's electron transport chain at metabolic peak points. A preset metabolic extreme value alarm threshold is set by adding a special degrading agent. Before the bacterial colony is dissolved, the water body to be treated is continuously monitored for 72 hours. The absolute value of the highest time-series second-order change rate during this period is extracted and calibrated by multiplying by 1.2. When the time-series second-order change rate shows a negative peak and the deviation of the negative peak from the potential decay benchmark value exceeds the metabolic extreme value alarm threshold, the system determines that the bottom anaerobic hydrolysis and fermentation process has reached the transient product peak. In response to this determination, the control unit cuts off the anaerobic settling circuit and starts time-series non-uniform pulsed microbubble aeration on the water body to be treated. At the same time, nitrate or hydrogen peroxide, which are electron acceptors, are simultaneously added to the water body to be treated during the aeration cycle. The above-mentioned physical equipment scheduling command, which is triggered by the time-series second-order change rate, cuts out mutually exclusive anaerobic fermentation windows and strong aerobic oxidation windows on the time axis, transforming the mass transfer resistance existing in the physical space into a metabolic relay that evolves in the time dimension.

[0043] During this non-uniform pulsed microbubble aeration cycle, the microbubble diameter remains between 10 μm and 50 μm. The aeration instantaneous surge in redox potential at the water-sediment interface drives specialized degrading bacteria to target and oxidize intermediate metabolites accumulated during the preceding acid-producing stage. Simultaneously, the control unit acquires the real-time redox potential recovery rate after the activation of the time-sequential non-uniform pulsed microbubble aeration. When the recovery rate falls below 5 mV / h, the control unit outputs a control command to linearly increase the instantaneous electron acceptor concentration until the recovery rate recovers to above 5 mV / h. The system utilizes this high-potential shock with a concentration feedback compensation mechanism to break the population suppression of indigenous dominant heterotrophic bacteria dependent on continuous substrate supply. Through the non-linear recovery of redox potential over time, it selectively inhibits the exponential proliferation of indigenous dominant heterotrophic bacteria. As the time-sequential pulse cycle with an anaerobic to aerobic ratio of 3:1 to 5:1 continues, facultative anaerobic bacteria... Engineered bacteria continuously hydrolyze recalcitrant organic matter at the bottom of the water body and mineralize and consume this organic matter in short-cycle strong oxidation pulses. The real-time transparency data of the water body to be treated exceeds the engineering acceptance standard of 50cm. The system ensures the colonization density and succession advantage of the special degradation bacteria in the open water environment by reshaping the temporal topological boundary of electron acceptor supply, and completes the synergistic bioremediation process for purifying polluted water. In this oxidation reshaping process, the overall redox potential gradient jumps dramatically. Its physical essence comes from the instantaneous surge in the concentration of dissolved oxygen (DO) molecules and reactive oxygen free radicals (ROS) in the boundary layer of the microenvironment. These high-energy electron acceptor surface media enter the cytoplasm of the special degradation bacteria through transmembrane diffusion of the cell membrane. Together with the substrate accumulated by anaerobic acid production, they act as biochemical induction signals to activate the transcription and expression of their specific oxygenase genes. Thus, the physical transformation of the overall potential to the surface enzymatic reaction is completed through the transfer of intracellular material flow.

[0044] Example 2: In a 500L lake sediment-water interface simulation reactor, a 15cm thick layer of sediment taken from the pollution site was laid at the bottom, covered with a 35cm thick layer of water to be treated. The reactor was equipped with an oxidation-reduction potential sensor with a measurement range of -1000mV to 1000mV and a resolution of 0.1mV, and a water temperature sensor with a temperature control accuracy of 0.1℃. A diurnal temperature fluctuation of 15℃ to 25℃ was applied to the outer water bath jacket of the reactor. Gaussian white noise with a signal-to-noise ratio of 20dB was superimposed on the raw signal of the oxidation-reduction potential sensor to simulate actual hydrodynamic disturbances. The system sampling period was set to balance the capture of transient metabolic peaks with the reduction of data processing load. When the water environment temperature decreased, causing a slowdown in the biochemical reaction rate, the high-frequency components of the signal decreased, and the sampling period was widened to reduce system power consumption. When the biochemical reaction activity increased, the sampling period was shortened. To avoid signal aliasing under the Nyquist sampling theorem constraint, the control unit selects 10s as the standard sampling period covering the entire temperature fluctuation range. The reactor is kept in an anaerobic, static state for 72 hours. The control unit extracts real-time redox potential data mixed with Gaussian white noise, uses a low-pass filter algorithm to remove high-frequency disturbances, and merges the real-time water temperature data into the preset Arrhenius kinetic equation. The open water sediment environment exhibits spatial heterogeneity. The sensor array is arranged in a two-dimensional spatial grid along the sediment surface. The control unit synchronously reads the local potential values ​​of each grid node to calculate the global median, removes singular node values ​​that deviate from the median by a set proportion, and establishes the arithmetic mean of the remaining node values ​​as the real-time redox potential data input to the control logic. Based on the theoretical model of exponential fluctuation of reaction rate with temperature, the control unit executes the conversion logic: the control unit uses the formula... The baseline value is refreshed periodically, whereby... Represents the real-time potential decay reference value; The calibrated potential decay rate at room temperature (20°C) in Example 4 is representative. The dimensionless constant representing the Arrhenius correction coefficient is constrained to the range of 1.02 to 1.08. It represents the real-time water temperature, and the real-time metabolic correction factor corrects the nonlinear sensitivity of biochemical reaction rates to temperature fluctuations, outputting a smooth potential decay benchmark value.

[0045] To eliminate the logical gap in the algorithm caused by cross-dimensional comparison between the first-order velocity feature (mV / h) and the second-order acceleration feature (mV / h²), a differential dimension reduction mapping logic was deployed within the control unit. This logic transforms the real-time calculated potential decay benchmark value from a first-order slope into a corresponding temporal acceleration benchmark feature by dividing it by a preset standard sampling period. The deviation used for subsequent extreme value determination is the algebraic difference between the detected negative peak value and the mapped temporal acceleration benchmark feature in the same dimension. During the static monitoring period, the highest temporal second-order rate of change generated by the bottom anaerobic hydrolysis fermentation process is determined. The absolute value is recorded as 2.5 mV / h². Based on the physical fact that direct differential amplification amplifies high-frequency disturbances in the data, the control unit extracts the filtered redox potential from three consecutive sampling cycles and performs discrete central difference calculation. The difference steps are as follows: the control unit adds the current cycle potential value to the potential values ​​of the previous two cycles, subtracts twice the potential value of the previous cycle, and then divides by the square of the sampling cycle duration to generate the second-order rate of change of the calculation window. The control unit multiplies this value by an engineering coefficient of 1.2 and calibrates the preset metabolic extreme alarm threshold to -3.0 mV / h². The above calibration procedure transforms empirical judgment into a wave-based calculation based on the intrinsic physical quantities of water. The quantitative criteria for dynamic operation were used to divide the system into four independently operating parallel sample groups to verify the objective effectiveness of time-sequential non-uniform pulsed microbubble aeration and parameter boundaries. The first control group used continuous aeration to maintain a constant dissolved oxygen process. The second control group had a 1:1 time ratio of anaerobic to aerobic phases in a single aeration pulse cycle, which was outside the lower limit of the specified range. The third control group had an 8:1 time ratio of anaerobic to aerobic phases, which was outside the upper limit of the specified range. The experimental group had a 4:1 time ratio of anaerobic to aerobic phases and simultaneously added nitrate, which acts as an electron acceptor, during the aeration cycle. In the specific addition control stage, the system utilized a submerged section... The UV / Vis multi-parameter water quality spectral probe captured the characteristic spectral absorption data of the water body in real time and converted it into the real-time monitoring value of total organic carbon based on the built-in partial least squares regression algorithm. The dosing system has a pre-calibrated piecewise proportional correspondence matrix. The control unit directly retrieves the corresponding output power parameter of the drug solution in the mapping matrix based on the real-time monitoring value, so that the initial concentration gradient of nitrate is accurately matched with the current organic carbon equivalent in the water body. After 120 hours of operation, the experimental group monitored a negative peak value of -3.2mV / h² for the second-order change rate of time. The deviation of this value from the potential decay reference value exceeded -3.When the metabolic extreme value alarm threshold of 0mV / h² is reached, the control unit cuts off the anaerobic settling circuit and starts the time-sequential non-uniform pulsed microbubble aeration. The microbubble diameter is maintained in the range of 10μm to 50μm. Micron-sized bubbles have weak buoyancy and are prone to horizontal drift with the stratosphere water flow. The system lays a bottom jet pipe network 10cm to 15cm above the bottom sediment surface. The control unit adjusts the output head of the aeration blower to maintain the local flow velocity at the nozzle greater than the shear rate of the bottom water flow, driving the microbubbles to penetrate the fluid boundary layer and attach to the bottom sediment surface. In the nanosecond-level instant of the violent contraction and eventual rupture of microbubbles at the sediment interface, surface cavitation and localized ultrasonic jets are released into the surrounding fluid medium. This concentrated burst of transient surface tension potential energy penetrates the biofilm pores that overall hydrodynamics cannot reach, providing instantaneous, extremely high-frequency localized physical shear forces at the micron-scale of cells. Relying on the repeated impacts of these microjet streams, the interwoven extracellular polymeric material (EPS) network structure within the indigenous dominant heterotrophic bacterial micelles is physically severed, achieving in-situ physical stripping of the stubbornly adhered layer.

[0046] During the aerobic oxidation window in the experimental group, microbubble aeration generated a surge in redox potential gradient at the sediment interface. The control unit continuously acquired the potential recovery rate. The initial potential recovery rate was measured at 2.4 mV / h, below the system lower limit of 5.0 mV / h. This quantitative characteristic indicated that the rate at which the indigenous heterotrophic bacteria consumed electron acceptors was greater than the targeted oxidation rate of the specialized degrading bacteria. The control unit then output control commands to linearly increase the instantaneous nitrate dosage concentration in 2.0 mg / L increments until… The pH level recovered and stabilized at 6.2 mV / h. In the first control group, a strong oxidizing environment was maintained, allowing the dominant indigenous heterotrophic bacteria to occupy the ecological niche, and the abundance of specialized degrading bacteria remained at 12,000 CFU / mL. In the second control group, the aerobic phase was too large, resulting in insufficient accumulation of intermediate metabolites in the acid-producing stage at the bottom layer, and the abundance of specialized degrading bacteria decreased to 35,000 CFU / mL. In the third control group, the anaerobic phase was too long, leading to a large accumulation of intermediate organic acids that caused a non-linear drop in the system's pH value. Due to acid inhibition, the specialized degrading bacteria population declined, with an abundance of only 41,000 CFU / mL. The experimental group, relying on a concentration feedback compensation mechanism and a 4:1 time-phased pulse cycle, drove the abundance of specialized degrading bacteria to cross the exponential growth phase and reach a saturation plateau region of 45,000,000 CFU / mL. The gradient characteristics confirm that the time ratio of 3:1 to 5:1 constitutes the optimal boundary that balances acid-producing fermentation and targeted oxidation. After the system ran continuously for 30 days, the measured water transparency data of each group were extracted. The water transparency of the first control group was 28 cm, the water transparency of the second control group was 35 cm, the water transparency of the third control group was 31 cm, and the water transparency of the experimental group reached 62 cm, exceeding the engineering acceptance standard of 50 cm. The non-uniform pulsed microbubble aeration and electron acceptor concentration feedback regulation mechanism triggered by the second-order change rate of time with temperature compensation, under dynamic conditions including diurnal temperature difference and hydrodynamic noise, segmented the time window of anaerobic fermentation and aerobic oxidation, suppressed the proliferation of native dominant heterotrophic bacteria, and established the dominant position of special degradation bacteria in the colonization and succession of polluted water bodies.

[0047] Example 3: The water body to be treated is subjected to flow velocity impact and resuspension of bottom sediment. The internal suspended particles collide with the sensor electrode surface, causing dynamic impedance fluctuations. This results in transient noise in the real-time oxidation-reduction potential data. Conventional low-pass filtering algorithms produce signal phase lag, masking the temporal second-order rate of change characterizing the bottom anaerobic hydrolysis and fermentation process. The sensor array collects real-time oxidation-reduction potential data of the water body to be treated. The control unit receives this real-time oxidation-reduction potential data and constructs a sliding data calculation window containing 6 sampling periods. The control unit removes the highest and lowest value data points in the sliding data calculation window, accumulates the remaining 4 data points and divides them by 4 to calculate the average value of the window. This average value of the window is established as the filtered oxidation-reduction potential at the current moment. This removal logic filters out transient potential jumps caused by bubble bursting and particle impact, and outputs a potential decay reference value without phase delay.

[0048] During the strong aerobic oxidation window, the control unit activates the dosing pump to inject hydrogen peroxide into the water to be treated, causing a surge in the redox potential gradient at the sediment interface. The control unit calculates the actual rise slope of the filtered redox potential over time and determines it as the potential recovery rate. The control unit sets the target recovery rate threshold to 5.0 mV / h. When the potential recovery rate is less than 5.0 mV / h, the control unit calculates the difference between 5.0 mV / h and the potential recovery rate, multiplies this difference by a proportional coefficient of 0.5, and calculates the compensation increment for the dosing pump drive frequency. The control unit then sends a control command containing this compensation increment to the frequency converter of the dosing pump. The instantaneous injection flow rate of hydrogen peroxide is increased, and the amount of hydrogen peroxide injected increases monotonically with the compensation increment. This compensates for the consumption of electron acceptors caused by the release of reducing substances from the bottom sediment due to hydraulic resuspension, so that the potential recovery rate rises to above 5.0 mV / h. After 48 hours of operation, the water transparency data of the treatment area acquired by the sensor remains at 55 cm. The potential acquisition loop with sliding rejection characteristics and the feedforward dosing control link based on the difference in potential recovery rate eliminate the noise of electrode mechanical collision and parameter drift caused by the release of reducing substrates. It also divides the time window of anaerobic fermentation and aerobic oxidation, ensuring the dominant succession of special degradation bacteria in the hydrodynamic disturbance environment.

[0049] Example 4: When the system faces initial deployment conditions, a closed bypass test reactor is constructed by extracting mixed water samples from the target area and surface sediment. The water bath temperature control module keeps the internal water temperature of the closed bypass test reactor constant at the standard reference temperature. The control unit cuts off the external electron acceptor addition circuit. The oxidation-reduction potential sensor continuously collects the initial potential decrease sequence for 48 hours. The control unit calculates the linear fitting slope of the potential decrease curve within this time window. The control unit extracts the absolute value of the linear fitting slope and determines it as the room temperature potential decay rate of the water body to be treated at the standard reference temperature.

[0050] The control unit adjusts the isothermal parameters of the closed bypass test reactor to establish a temperature gradient sequence. The closed bypass test reactor is left to stand for 12 hours at each temperature gradient node. The redox potential sensor synchronously collects the corresponding real-time redox potential decay slope. The control unit calculates a linear regression equation with the reciprocal of the absolute temperature as the independent variable and the natural logarithm of the corresponding real-time redox potential decay slope as the dependent variable. The control unit extracts the absolute value of the slope of the linear regression equation and determines it as the Arrhenius correction coefficient. The control unit writes the Arrhenius correction coefficient and the room temperature potential decay rate into the storage register of the main control system to generate the initial input parameters for calculating the potential decay benchmark value.

[0051] Example 5: In a water body undergoing long-term continuous operation with internal suspended solids concentrations fluctuating by orders of magnitude, a dynamically varying biofilm layer forms on the sensor electrode surface. This biofilm layer constitutes a physical isolation barrier and induces low-frequency baseline drift in real-time oxidation-reduction potential (ORP) data. The control unit initiates an offline optimization calibration process, extracts water samples from the target area to construct a standard simulated flow channel with a reference electrode, and starts a dosing pump to inject electron acceptors into the standard simulated flow channel using a flow array with an arithmetic gradient. The control unit continuously collects the actual ORP recovery rate at different injection flow rates, calculates the root mean square (RMS) error between the preset theoretical recovery rate and the actual ORP recovery rate at the corresponding flow rate, and initiates an traversal search logic with the objective function of minimizing the RMS error to extract a specific flow rate mapping slope that minimizes the objective function value. The control unit determines the slope of a specific flow rate mapping as the proportional coefficient for calculating the incremental compensation of the dosing pump drive frequency. This offline optimization calibration process transforms the core constants contained in the dosing feedback logic into engineering measured indicators based on the on-site hydrodynamic characteristics. To compensate for the low-frequency baseline drift, the control unit uses an external metering pump to instantaneously inject sodium acetate solution with a known concentration gradient into the sediment interface as a carbon source pulse. The biofilm on the sensor surface is stimulated by this easily degradable substrate, which rapidly changes its metabolic activity, causing the potential probe to acquire a transient response characteristic curve that first drops sharply and then gradually recovers. The system extracts the maximum tangent slope of the attenuation segment of the curve as the probe differential value and uses it as a dynamic bias term to compensate the current measurement data obtained by the probe in real time. Through feedforward correction, the physical response hysteresis and baseline deviation caused by the biofilm are directly eliminated.

[0052] The control unit activates the data reconstruction mechanism, accumulating the total number of operating cycles of time-series non-uniform pulsed microbubble aeration. When the total number of operating cycles reaches the preset maintenance trigger threshold, the control unit suspends the current cycle's microbubble aeration and electron acceptor delivery process, and activates the ultrasonic cleaning unit mounted on the sensor array to generate a high-frequency cavitation effect to peel off the bio-attached layer on the electrode surface. After the cleaning action is completed, the control unit maintains the system in a passive static state, extracts the real-time oxidation-reduction potential data within a continuously set time period in this passive static state, calculates the time series moving average of the real-time oxidation-reduction potential data, and calculates the difference between the time series moving average and the potential decay benchmark value measured at the initial deployment. The aforementioned difference is extracted and determined as the baseline offset compensation amount. In subsequent water body monitoring, the control unit superimposes the baseline offset compensation amount on all newly acquired real-time oxidation-reduction potential data and outputs calibrated real-time oxidation-reduction potential data. This data reconstruction procedure eliminates the underlying signal drift caused by sensor dynamic aging and interface contamination, and maintains the long-term effectiveness of the time-series second-order rate of change trigger criterion.

[0053] It will be apparent to those skilled in the art that the present invention is not limited to the details of the exemplary embodiments described above, and that the present invention can be implemented in other specific forms without departing from the spirit or essential characteristics of the present invention.

[0054] Finally, it should be noted that the above embodiments are only used to illustrate the technical solutions of the present invention and are not intended to limit it. Although the present invention has been described in detail with reference to preferred embodiments, those skilled in the art should understand that modifications or equivalent substitutions can be made to the technical solutions of the present invention without departing from the spirit and scope of the technical solutions of the present invention.

Claims

1. A synergistic bioremediation process for purifying polluted water bodies, characterized in that, Includes the following steps: Step S1: Obtain real-time oxidation-reduction potential data and real-time water temperature data of the water body to be treated; Step S2: Use real-time water temperature data to perform kinetic compensation on the preset room temperature potential decay rate, and establish a potential decay benchmark value that characterizes the metabolic intensity of the microbial community inside the water body to be treated. The compensation process corrects the nonlinear sensitivity of the biochemical reaction rate to temperature fluctuations through the Arrhenius kinetic equation. Step S3: Calculate the time-series second-order rate of change of real-time redox potential with sampling time to identify the acceleration characteristics of the electron transport chain in water at the metabolic peak point. Step S4: Monitor the second-order change rate over time. When it shows a negative peak and the deviation of the negative peak from the potential decay reference value exceeds the preset metabolic extreme value alarm threshold, turn on the non-uniform pulsed microbubble aeration to the water body to be treated to interrupt the original anaerobic fermentation steady state environment. Step S5: During the aeration cycle of time-uniform pulsed microbubble aeration, an electron acceptor is simultaneously introduced into the water to be treated. The dramatic gradient jump in redox potential generated at the interface between the water and the sediment during aeration drives the special degradation bacteria to target and oxidize the intermediate metabolites accumulated in the previous acid production stage. Through the nonlinear recovery of redox potential over time, the exponential proliferation of the indigenous dominant heterotrophic bacteria is selectively inhibited.

2. The synergistic bioremediation process for purifying polluted water bodies according to claim 1, characterized in that, The process of obtaining the potential decay benchmark value in step S2 includes: step S21, calculating the real-time metabolic correction factor based on the real-time water temperature and the preset Arrhenius correction coefficient; step S22, the real-time metabolic correction factor is positively correlated with the real-time water temperature, and by adjusting the temperature sensitivity of the biochemical reaction rate, the benchmark decay slope under 20℃ conditions is converted into a potential decay benchmark value that matches the current operating conditions, so that the negative peak determination criterion in step S4 has seasonal adaptability.

3. The synergistic bioremediation process for purifying polluted water bodies according to claim 1, characterized in that, In step S4, the parameters for time-sequential non-uniform pulsed microbubble aeration are limited to: microbubble diameter of 10. m to 50 m, the time ratio of the anaerobic phase to the aerobic phase in a single aeration pulse cycle is set to 3:1 to 5:1; by maintaining a long-cycle reducing environment, special degrading bacteria are induced to secrete oxygenases targeting recalcitrant organic matter, and short-cycle strong oxidation pulses are used to complete substrate mineralization.

4. The synergistic bioremediation process for purifying polluted water bodies according to claim 1, characterized in that, The process of adding electron acceptor in step S5 includes: obtaining the real-time redox potential at the potential recovery rate after the start of sequential non-uniform pulsed microbubble aeration; when the potential recovery rate is lower than the preset 5mV / h, linearly increasing the instantaneous concentration of electron acceptor until the potential recovery rate recovers to above 5mV / h, so as to eliminate the mass transfer resistance at the sediment interface.

5. The synergistic bioremediation process for purifying polluted water bodies according to claim 1, characterized in that, It also includes a sensor calibration step: Step S6, obtain the probe micro-differential value of the potential probe that collects real-time redox potential data; Step S7, use the potential transient response characteristic curve induced by carbon source pulse injection, combined with the probe micro-differential value, to complete the in-situ drift compensation of the potential probe, so as to eliminate the systematic deviation caused by the biofilm adhesion on the surface of the potential probe on the redox potential measurement accuracy.

6. The synergistic bioremediation process for purifying polluted water bodies according to claim 3, characterized in that, The timing control rules for non-uniform pulsed microbubble aeration include: monitoring the highest potential value at the end of the aerobic phase; when the highest potential value shows a monotonically decreasing trend within three consecutive aeration pulse cycles, automatically shortening the duration of the anaerobic phase in subsequent pulse cycles and simultaneously increasing the frequency of electron acceptor delivery to prevent excessive acidification of the water.

7. The synergistic bioremediation process for purifying polluted water bodies according to claim 1, characterized in that, In step S5, the physical shear force generated by time-sequential non-uniform pulsed microbubble aeration is used to break up the bacterial floc structure formed by the indigenous dominant heterotrophic bacteria in the water to be treated; by peeling off the indigenous dominant heterotrophic bacteria, the active attachment sites on the surface of the bottom sediment of the water to be treated are exposed, providing physical space for the amplification of special degrading bacteria.

8. The synergistic bioremediation process for purifying polluted water bodies according to claim 1, characterized in that, The electron acceptor is perchlorate, nitrate, or hydrogen peroxide. The concentration of the electron acceptor is matched with the concentration gradient based on the real-time monitoring value of the total organic carbon in the water to be treated. The electron acceptor release is controlled at the moment when the negative extreme value of the second-order rate of change occurs, thus realizing the dynamic coupling between chemical agent addition and microbial metabolic rhythm.

9. The synergistic bioremediation process for purifying polluted water bodies according to claim 1, characterized in that, The process after step S5 also includes: acquiring real-time transparency data of the water body to be treated; when the real-time transparency data reaches 50cm or more, reducing the output power of the time-series non-uniform pulsed microbubble aeration, and utilizing the oxygen secretion effect of aquatic plant roots to maintain the steady state of the redox potential of the water body to be treated under low oxygen load.

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