Wastewater treatment regulation and control method and system in gypsum-to-acid clean production

Abstract

The invention provides a wastewater treatment regulation and control method and system in gypsum-to-acid clean production, and relates to the technical field of industrial wastewater treatment.The method comprises the steps that flue gas washing wastewater, equipment cooling wastewater and ground flushing wastewater are put into a regulating tank to be mixed, and mixed wastewater is formed; monitoring the pH value of the mixed wastewater in real time to obtain a current pH monitoring result; based on the current pH monitoring result, dynamically adjusting the adding amount of lime milk, and neutralizing the mixed wastewater to obtain neutralized wastewater; setting a detection cross section perpendicular to the water flow direction at an outlet of a conveying pipeline through which the neutralized wastewater enters the sedimentation tank; on a detection cross section, three fixed sampling positions are dynamically set at the center position of the pipeline, the upper side away from the pipe wall by one fourth of the radius and the lower side away from the pipe wall by one fourth of the radius respectively. According to the invention, efficient and stable standard treatment and cyclic utilization of the gypsum acid-making wastewater are realized.

Description

TECHNICAL FIELD

[0001] The present application relates to the technical field of industrial wastewater treatment, in particular to a wastewater treatment regulation method and system in gypsum-based acid clean production. BACKGROUND

[0002] As a key technical path for industrial solid waste resource utilization, the gypsum-based acid process occupies a core position in the recycling and treatment of industrial by-product gypsum such as phosphogypsum and desulfurization gypsum. However, multiple-source heterogeneous wastewater is inevitably produced in the production process of this process, mainly including three categories of flue gas washing wastewater, equipment cooling wastewater and ground washing wastewater: flue gas washing wastewater presents strong acidity due to the absorption of acidic components and suspended mineral dust in the kiln gas, and contains fluoride ions, sulfate ions and coal tar and other colloidal substances; the water quality of equipment cooling wastewater is relatively mild but the water volume fluctuates greatly; the concentration of suspended solids and calcium ions in ground washing wastewater is unstable due to the inclusion of raw material residues.

[0003] The current mainstream wastewater treatment method in the industry faces many technical bottlenecks in actual operation: first, the homogenization of water quality is insufficient, for example, the adjustment tank mainly uses a single containing space for natural mixing, and the three types of wastewater are prone to stratification due to differences in density and acidity, resulting in uneven distribution of mixed wastewater quality. Second, the neutralization reaction regulation is extensive: for example, the lime milk dosage is calculated based on the single-point pH monitoring value at the outlet of the adjustment tank, which does not take into account the spatial distribution difference of water quality and lacks a pH closed-loop correction mechanism after the reaction, relying only on static control of the theoretical dosage, resulting in a large pH fluctuation range of the wastewater after neutralization, and even exceeding the standard range of 6 to 9 in some periods. Third, the precipitation process lacks prediction: before the neutralized wastewater enters the sedimentation tank, the water quality parameters are monitored only by single-point sampling at the end of the pipeline, which cannot reflect the concentration gradient difference of the water cross section; and the existing technology does not establish a correlation between water quality parameters and sedimentation behavior, so the sedimentation tank operating parameters can only be adjusted passively after the effluent exceeds the standard. Fourth, the resource recycling rate is limited: due to unstable sedimentation effect, the residual amount of suspended solids and ions in the clear liquid is high, and only 30% to 50% of the effluent can be recycled for the flue gas washing process, the rest needs to be treated by reverse osmosis and other advanced treatment processes, resulting in high treatment cost, and the concentration process of concentrated water is prone to secondary pollution of salt mud.

[0004] With the strict control of fluoride emission limits and the improvement of clean production requirements by the state, the passive treatment and post-repair mode of traditional processes have been difficult to meet the environmental protection needs of the gypsum-based acid industry. SUMMARY

[0005] The technical problem to be solved by the present application is to provide a wastewater treatment regulation method and system in gypsum-based acid clean production, which can solve the problems of low treatment efficiency, unstable effluent and limited resource recycling rate of traditional processes, and realize efficient, stable and standard-compliant treatment and recycling of gypsum-based acid wastewater.

[0006] To solve the above-mentioned technical problems, the technical solution of the present invention is as follows: In a first aspect, a method for wastewater treatment and control in the clean production of gypsum-based acid manufacturing, the method comprising: The wastewater from flue gas scrubbing, equipment cooling, and floor washing is mixed in an equalization tank to form a mixed wastewater. The pH value of the mixed wastewater is monitored in real time to obtain the current pH monitoring results; Based on the current pH monitoring results, the amount of lime slurry added is dynamically adjusted, and the mixed wastewater is neutralized to obtain neutralized wastewater. At the outlet of the conveying pipe from the neutralized wastewater into the sedimentation tank, a detection section is set perpendicular to the water flow direction. On the detection section, three fixed sampling positions are dynamically set at the center of the pipe, the upper side at a quarter radius from the pipe wall, and the lower side at a quarter radius from the pipe wall. The three key water quality parameters of pH value, calcium ion concentration and fluoride ion concentration are acquired simultaneously at the three sampling positions. Based on three key water quality parameters, a virtual spatial configuration is constructed, and the real-time characterization parameters of the spatial configuration are calculated. Based on the real-time characterization parameters, a comprehensive correction value is obtained. Based on the comprehensive correction value, the three key water quality parameters are jointly corrected to obtain a set of corrected parameters. Based on the corrected parameters, a forward-looking judgment is made on the formation state and settling trend of the sediment in the sedimentation tank; based on the results of the forward-looking judgment, the influent rate of the sedimentation tank is adjusted in advance or flocculants are added to form sedimentation influent with optimized properties. The optimized influent is placed in a sedimentation tank and treated by natural sedimentation to obtain a clear liquid that meets the standards. The clear liquid that meets the standards is collected and either discharged directly or reused in the production process.

[0007] Furthermore, the flue gas scrubbing wastewater, equipment cooling wastewater, and floor washing wastewater are introduced into a regulating tank for mixing to form mixed wastewater, including: The wastewater from flue gas scrubbing, equipment cooling, and floor washing is introduced into the designated containment area of ​​the equalization tank through independent conveying pipelines. Real-time monitoring of the instantaneous flow rate and pH value of various types of wastewater in the designated containment area; Based on the monitoring results of instantaneous flow rate and pH value, the delivery rate of various types of wastewater flowing into the main mixing zone of the equalization tank is dynamically adjusted; In the main mixing zone of the equalization tank, various types of wastewater that are fed in according to the conveying rate are forcibly mixed and agitated. Forced mixing and agitation promotes the full interaction and diffusion of wastewater with different properties, ultimately forming a mixed wastewater with a relatively uniform water quality distribution.

[0008] Furthermore, the pH value of the mixed wastewater is monitored in real time to obtain the current pH monitoring results, including: Inside the main mixing zone of the equalization tank, a spatial array of monitoring points consisting of multiple pH sensors is arranged; By using a spatial array of monitoring points, multiple real-time pH readings of the mixed wastewater at different spatial locations are collected simultaneously. Based on the values ​​of multiple real-time pH readings and their corresponding spatial relationships, a dispersion index is calculated to characterize the pH distribution equilibrium within the entire main mixing zone. Based on the dispersion index, the weighting of the pH readings involved in the final calculation is dynamically adjusted. By weighted fusion of multiple real-time pH readings, a current pH monitoring result that can represent the overall acid-base state of the mixed wastewater is obtained.

[0009] Furthermore, based on the current pH monitoring results, the dosage of lime slurry is dynamically adjusted, and the mixed wastewater is neutralized to obtain neutralized wastewater, including: Based on the current pH monitoring results, the required theoretical amount of lime slurry is calculated by combining the preset target pH range. Based on the theoretical dosage of lime slurry, the lime slurry is injected into the neutralization reaction zone by adjusting the instantaneous flow rate of lime slurry addition; Within the neutralization reaction zone, stirring ensures that the lime slurry and the mixed wastewater come into full contact and undergo a neutralization reaction. During the neutralization reaction, the instantaneous pH value of the effluent from the neutralization reaction zone is monitored in real time and compared with the target pH range; Based on the comparison results, the amount of lime slurry added was finely adjusted in a closed loop to ensure that the pH value of the effluent remained stable within the target pH range; the effluent with a stable pH value within the target pH range was identified as qualified neutralized wastewater.

[0010] Furthermore, at the outlet of the conveying pipe from which the neutralized wastewater enters the sedimentation tank, a detection section is set perpendicular to the water flow direction. On this detection section, three fixed sampling points are dynamically set at the center of the pipe, the upper side at a quarter radius from the pipe wall, and the lower side at a quarter radius from the pipe wall. Simultaneously, three key water quality parameters—pH value, calcium ion concentration, and fluoride ion concentration—are acquired at these three sampling points. The qualified neutralized wastewater flows through the pre-designed conveying pipeline; At the outlet of the conveying pipeline, a detection section is established perpendicular to the direction of wastewater flow; On the inspection section, the center position of the pipe, the upper position at a quarter radius from the pipe wall, and the lower position at a quarter radius from the pipe wall are precisely marked as three specific spatial points; The three specific spatial locations are set as fixed sampling locations; the pH value, calcium ion concentration and fluoride ion concentration at the three sampling locations are collected synchronously within the set time window using a multi-parameter water quality sensor. The pH value, calcium ion concentration, and fluoride ion concentration collected simultaneously were summarized into three key water quality parameters.

[0011] Furthermore, based on three key water quality parameters, a virtual spatial configuration is constructed, and the real-time characterization parameters of the spatial configuration are calculated. Based on these real-time characterization parameters, a comprehensive correction value is obtained. Based on this comprehensive correction value, the three key water quality parameters are jointly corrected to obtain a set of corrected parameters, including: Acquire spatial location information of three sampling sites and the corresponding three key water quality parameters; Based on the spatial location information of the three sampling points, a virtual reference plane is constructed; the key water quality parameters corresponding to the sampling point located at the center of the pipeline are mapped to a theoretical projection point on the virtual reference plane. Calculate the overall deviation between the actual key water quality parameters at the sampling point at the center location and the theoretical projection point; based on the overall deviation, generate an overall correction value; Based on the comprehensive correction value, the original key water quality parameters obtained synchronously from the three sampling locations are jointly corrected. Through joint correction processing, a set of corrected parameters that can more accurately reflect the overall properties of the water body are obtained.

[0012] Furthermore, based on the corrected parameters, a forward-looking assessment of the formation state and settling trend of the sediment in the sedimentation tank is made; based on the results of the forward-looking assessment, the influent rate of the sedimentation tank is adjusted in advance or flocculant is added to form optimized sedimentation influent, including: The corrected parameters were compared and analyzed with the preset empirical thresholds for precipitate formation and sedimentation. Based on the comparative analysis results, the formation rate and settling velocity of sediment in the sedimentation tank under the current water quality conditions are predicted. Based on the predicted generation rate and settling velocity, determine whether the operating conditions of the sedimentation tank need to be adjusted; When the predicted settling velocity is lower than the formation rate, reduce the influent rate of the sedimentation tank or start the flocculant addition process. By adjusting the influent rate or adding flocculants, the properties of the wastewater to be treated are optimized, resulting in optimized precipitated influent.

[0013] Furthermore, the optimized influent is placed in a sedimentation tank for natural settling to obtain a clarified liquid that meets the standards. This clarified liquid is collected for direct discharge or reuse in the production process, including: The optimized influent is introduced into the uniform water distribution zone of the sedimentation tank; within the sedimentation tank, suspended solids and the generated CaF2 and Ca3(PO4)2 precipitates are naturally separated by gravity. After the set set settling time is reached, water samples are collected from the clear water area at the top of the sedimentation tank, and the turbidity and key ion concentration of the water samples are monitored. The monitoring results are compared and verified with the preset emission or reuse standards; When the verified monitoring results meet the standards, the qualified clear liquid is collected for direct discharge or reuse in the production process. When the verified monitoring results do not meet the standards, a portion of the clarified liquid is returned to the equalization tank for further treatment.

[0014] Secondly, a wastewater treatment and control system for clean production of gypsum-based acid manufacturing includes: The monitoring module is used to mix flue gas scrubbing wastewater, equipment cooling wastewater and floor flushing wastewater in an equalization tank to form mixed wastewater; and to monitor the pH value of the mixed wastewater in real time to obtain the current pH monitoring results. The adjustment module dynamically adjusts the amount of lime slurry added based on the current pH monitoring results, and obtains neutralized wastewater by neutralizing the mixed wastewater. The module sets up a detection section perpendicular to the water flow direction at the outlet of the conveying pipe from which the neutralized wastewater enters the sedimentation tank. On the detection section, three fixed sampling positions are dynamically set at the center of the pipe, the upper side at a quarter radius from the pipe wall, and the lower side at a quarter radius from the pipe wall. The three key water quality parameters of pH value, calcium ion concentration and fluoride ion concentration are acquired simultaneously at the three sampling positions. The module constructs a virtual spatial configuration based on three key water quality parameters and calculates the real-time characterization parameters of the spatial configuration. Based on the real-time characterization parameters, a comprehensive correction value is obtained. Based on the comprehensive correction value, the three key water quality parameters are jointly corrected to obtain a set of corrected parameters. The judgment module makes a forward-looking judgment on the formation state and settling trend of the sediment in the sedimentation tank based on the corrected parameters; based on the results of the forward-looking judgment, it adjusts the influent rate of the sedimentation tank in advance or adds flocculant to form sedimentation influent with optimized properties. The processing module introduces the optimized precipitated influent into a sedimentation tank, where it undergoes natural sedimentation to obtain a clear liquid that meets the standards. The clear liquid that meets the standards is then collected for direct discharge or reuse in the production process.

[0015] Thirdly, a computing device, comprising: One or more processors; A storage device for storing one or more programs that, when executed by one or more processors, cause the one or more processors to implement the method.

[0016] Fourthly, a computer-readable storage medium storing a program that, when executed by a processor, implements the method.

[0017] The above-described solution of the present invention has at least the following beneficial effects: By employing technologies such as dynamic rate regulation and forced mixing of multi-source wastewater, spatial array monitoring and weighted fusion of pH in mixed wastewater, closed-loop fine-tuning of pH in neutralization reaction, simultaneous three-point sampling of pipeline cross-sections before sedimentation and joint correction of parameter virtual configuration, and forward-looking prediction and control of sedimentation generation and settling trends based on correction parameters, this approach effectively overcomes the technical problems in traditional gypsum-based acid production wastewater treatment processes, including insufficient homogenization of multi-source wastewater mixing, extensive pH fluctuations due to coarse control of neutralization reaction, lack of spatial representativeness in water quality monitoring before sedimentation, passive adjustment due to lack of prediction during sedimentation, and limited resource recovery rate. This results in uniform and stable distribution of mixed wastewater quality, precise pH control of wastewater after neutralization, optimized sedimentation reaction conditions, and significantly improved efficiency in the generation and settling of CaF2 and other precipitates. Ultimately, this leads to stable compliance of effluent fluoride concentration, a significantly increased clear liquid recovery rate, reduced wastewater treatment costs and secondary pollution risks, and the efficient and stable treatment and recycling of gypsum-based acid production wastewater. Attached Figure Description

[0018] Figure 1 This is a schematic flowchart of a wastewater treatment and control method in the clean production of gypsum-based acid production, provided by an embodiment of the present invention.

[0019] Figure 2 This is a schematic diagram of a wastewater treatment and control system in the clean production of gypsum-based acid production, provided by an embodiment of the present invention. Detailed Implementation

[0020] Exemplary embodiments of the present disclosure will now be described in more detail with reference to the accompanying drawings. While exemplary embodiments of the present disclosure are shown in the drawings, it should be understood that the present disclosure may be implemented in various forms and should not be limited to the embodiments set forth herein. Rather, these embodiments are provided so that this disclosure will be thorough and complete, and will fully convey the scope of the disclosure to those skilled in the art.

[0021] like Figure 1 As shown in the figure, an embodiment of the present invention proposes a wastewater treatment and control method in the clean production of gypsum-based acid manufacturing, the method comprising the following steps: Step 1: Mix the flue gas scrubbing wastewater, equipment cooling wastewater, and ground flushing wastewater in the equalization tank to form mixed wastewater; Step 2: Monitor the pH value of the mixed wastewater in real time to obtain the current pH monitoring results; Step 3: Based on the current pH monitoring results, dynamically adjust the amount of lime slurry added, and neutralize the mixed wastewater to obtain neutralized wastewater; Step 4: At the outlet of the conveying pipe from which the neutralized wastewater enters the sedimentation tank, a detection section is set perpendicular to the water flow direction. On the detection section, three fixed sampling positions are dynamically set at the center of the pipe, the upper side at a quarter radius from the pipe wall, and the lower side at a quarter radius from the pipe wall. The three key water quality parameters of pH value, calcium ion concentration and fluoride ion concentration are acquired simultaneously at the three sampling positions. Step 5: Based on the three key water quality parameters, construct a virtual spatial configuration and calculate the real-time characterization parameters of the spatial configuration; based on the real-time characterization parameters, obtain a comprehensive correction value; based on the comprehensive correction value, perform joint correction on the three key water quality parameters to obtain a set of corrected parameters; Step 6: Based on the corrected parameters, make a forward-looking judgment on the formation state and settling trend of the sediment in the sedimentation tank; according to the results of the forward-looking judgment, adjust the influent rate of the sedimentation tank in advance or add flocculant to form sedimentation influent with optimized properties. Step 7: Place the optimized precipitated influent into the sedimentation tank and obtain a clear liquid that meets the standards through natural sedimentation treatment; collect the clear liquid that meets the standards for direct discharge or reuse in the production process.

[0022] In this embodiment of the invention, mixing the three types of wastewater in an equalization tank results in a more uniform distribution of the mixed wastewater quality, providing a stable water quality foundation for subsequent treatment stages. Real-time monitoring of the pH value of the mixed wastewater allows for precise control of its overall acid-base state, enabling more targeted adjustments to the lime slurry dosage. Dynamically adjusting the lime slurry dosage based on pH monitoring results ensures a sufficient and stable neutralization reaction, maintaining the pH value of the neutralized wastewater within a suitable range. Setting three fixed sampling points at the outlet of the conveying pipeline and simultaneously acquiring parameters comprehensively reflects the concentration gradient differences across the water body, avoiding the limitations of single-point sampling. Constructing a virtual space configuration for joint correction of key water quality parameters improves parameter accuracy. Based on the corrected parameters, proactively judging the state and settling trend of sediment in the sedimentation tank and adjusting operating conditions in advance optimizes the properties of the influent, avoiding the problem of reactive adjustments after effluent exceeds standards. The final clarified liquid obtained through natural sedimentation is more likely to meet standards, allowing for direct discharge to meet environmental requirements or effective reuse in the production process, improving the efficiency and stability of wastewater treatment and enhancing the level of water resource recycling.

[0023] In a preferred embodiment of the present invention, step 1 above may include: Step 1.1: Flue gas scrubbing wastewater, equipment cooling wastewater, and floor washing wastewater are introduced into designated areas of the equalization tank via independent pipelines. Specifically, this includes: three independent rigid PVC pipeline sections are arranged parallel to each other along the length of the equalization tank at the inlet end, each corresponding to a specific type of wastewater. The first pipeline section connects to the end collection tank of the flue gas scrubbing wastewater, the second pipeline section connects to the main drainage pipe of the equipment cooling device, and the third pipeline section connects to the collection ditch of the floor washing wastewater. Simultaneously, a concrete retaining wall physically divides the equalization tank inlet area into three separate designated areas. Each area has an overflow outlet at the top and a drain valve at the bottom. The inlet of each area is sealed to the outlet of one of the pipeline sections via flanges, ensuring that the flue gas scrubbing wastewater, equipment cooling wastewater, and floor washing wastewater are stored separately in their respective areas after entering the equalization tank, preventing irregular premature mixing of the three types of wastewater before flow and water quality control.

[0024] Step 1.2 involves real-time monitoring of the instantaneous flow rate and pH value of various types of wastewater in the designated containment area. Specifically, this includes installing an instantaneous flow transmitter and an online pH electrode on the outlet pipe section of each designated containment area. The instantaneous flow transmitter utilizes electromagnetic induction and is installed at the horizontal straight section of the pipe to ensure the pipe is filled with wastewater and avoid interference from empty pipes. Its measurement range covers 0 to 50m. 3 / h, with an accuracy controlled within ±0.5%, to capture the instantaneous flow data of the corresponding wastewater before it flows into the main mixing zone in real time; the online pH electrode is made of glass electrode material, the probe is inserted into the pipe section and perpendicular to the water flow direction, the electrode response time is less than or equal to 2 seconds, and the measurement range is 0 to 14 pH, used to synchronously collect the real-time acid and alkalinity status of the corresponding wastewater at the outlet of the containment area; the output signals of all monitoring devices are transmitted to the field display instrument through signal lines, and the data is updated every 3 seconds.

[0025] Step 1.3: Based on the monitoring results of instantaneous flow rate and pH value, dynamically adjust the delivery rate of various wastewaters flowing into the main mixing zone of the equalization tank. Specifically, this includes: based on the acquired instantaneous flow rate and pH value data of the three types of wastewater, first calculate the proportion of the current instantaneous flow rate of each wastewater to the total planned mixing flow rate, and then combine this with the pH value of the flue gas scrubbing wastewater, where the pH value is usually between 2.0 and 4.0, to determine its acidity. The stronger the acidity, the lower the rate at which it flows into the main mixing zone needs to be, to avoid a sudden drop in pH of the mixed wastewater due to excessive single-flow volume. Based on this, a regulating valve is installed downstream of the flow transmitter of each receiving area outlet pipe section. The opening of the valve is adjusted manually or automatically, with an adjustment range of 0 to 100%, thereby changing the wastewater delivery rate. For example, when the instantaneous flow rate of the flue gas scrubbing wastewater reaches 15 m³ / h... 3When the pH value is 2.5, the corresponding valve opening is reduced from 50% to 30%, while the valve opening of the equipment cooling wastewater, whose pH value is usually between 7.0 and 8.0, is increased from 40% to 50% to balance the overall water volume and acid-base basis of the mixing system, ensuring that the three types of wastewater flow smoothly into the main mixing zone of the regulating tank in a preset ratio.

[0026] Step 1.4: In the main mixing zone of the equalization tank, the various types of wastewater flowing in at the conveying rate are forcibly mixed and agitated. Specifically, this includes: symmetrically installing two propeller-type agitators along the width of the tank at the center of the main mixing zone. The agitator blades have a diameter of 1.2m and an angle of 30°, and are installed at half the normal liquid level of the tank to ensure that the blades can simultaneously drive the water flow in both the upper and lower parts of the tank when rotating; after the three types of wastewater flow into the main mixing zone at the adjusted rate, the rotation speed of the agitator is adjusted according to the total amount of water flowing in; the effective volume of the main mixing zone is 50m³. 3 The liquid level is controlled at three-quarters full, and when the total water volume reaches 20m³... 3 At that time, the rotation speed was set to 60 r / min; the total water volume reached 30 m³. 3 At that time, the rotation speed increased to 90 r / min; the total water volume reached 37.5 m³. 3 At that time, the rotation speed was stabilized at 120 r / min; after the stirring device was started, it pushed the wastewater in the main mixing zone to form a counterclockwise vortex. The vortex caused the acidic water of flue gas scrubbing wastewater, the neutral water of equipment cooling wastewater, and the slag-containing water of ground washing wastewater to circulate in the pool, breaking the vertical stratification phenomenon caused by the density difference of the three types of wastewater. The density of the flue gas scrubbing wastewater is about 1.03 g / cm³. 3 The equipment cooling wastewater is approximately 1.00 g / cm³. 3 This promotes the initial contact and mixing of wastewater of different properties during the flow.

[0027] Step 1.5 involves forced mixing and agitation to promote full interaction and diffusion of wastewater with different properties, ultimately forming a relatively uniformly distributed mixed wastewater. Specifically, after continuous mixing for 15 to 20 minutes, three water quality sampling points are set up at the outlet, middle, and near the mixing device of the main mixing zone. A 500 mL sample of mixed water is taken from each sampling point, and the pH value, calcium ion concentration, and suspended solids (SS) concentration are measured. By comparing the test results from the three sampling points, the coefficient of variation for each indicator is calculated. The coefficient of variation is equal to the standard deviation multiplied by the average value multiplied by 100%. When the coefficient of variation for pH value is less than or equal to 0.3%, the coefficient of variation for calcium ion concentration is less than or equal to 2%, and the coefficient of variation for suspended solids concentration is less than or equal to 5%, it indicates that the acidic components, calcium ions, and suspended solids of the three types of wastewater have achieved full interaction and molecular diffusion under the eddy current, and the water quality parameters in different areas tend to be consistent. At this point, the water in the main mixing zone has formed a relatively uniformly distributed mixed wastewater, which will flow out through the guide channel at the outlet of the main mixing zone.

[0028] In this embodiment of the invention, three types of wastewater are introduced into designated areas of the equalization tank via independent pipelines. This avoids premature mixing of wastewater with different properties during transport, reducing the problem of uneven initial mixing. Real-time monitoring of the instantaneous flow rate and pH value of each type of wastewater allows for timely understanding of its real-time status, providing accurate data support for adjusting the transport rate. Dynamically adjusting the inflow rate of each type of wastewater into the main mixing zone based on the monitoring results optimizes the inflow ratio according to the differences in the properties of different wastewaters, further improving the rationality of mixing. Forced mixing and agitation of the wastewater in the main mixing zone breaks down the stratification that may occur due to differences in density and acidity, promoting full interaction and diffusion of wastewater with different properties. Ultimately, through this series of operations, the problem of uneven water quality distribution caused by traditional equalization tank mixing methods can be effectively solved, forming a relatively uniform mixed wastewater. This provides a stable and consistent water quality foundation for pH monitoring, neutralization treatment, and other stages, helping to improve the efficiency and stability of the entire wastewater treatment process.

[0029] In a preferred embodiment of the present invention, step 2 above may include: Step 2.1: Within the main mixing zone of the equalization tank, a spatial array of monitoring points consisting of multiple pH sensors is arranged. Specifically, this includes: planning the layout of the monitoring point spatial array within the main mixing zone of the equalization tank, taking into account the mixing range of the stirring device and the characteristics of the water flow in the tank; dividing the main mixing zone into three vertical regions—upper, middle, and lower—based on its spatial structure; and further dividing the area directly affected by the stirring device and the peripheral indirectly affected area based on the range of action of the stirring device; setting monitoring points within these regions to ensure that all points cover every corner of the main mixing zone, avoiding any potential dead zones in the water flow within the tank. This ensures that the monitoring points reflect the water quality in the central mixing area as well as the water quality in the peripheral areas, thus establishing a comprehensive monitoring point framework for collecting pH data from different spatial locations.

[0030] Step 2.2 involves synchronously collecting multiple real-time pH readings of the mixed wastewater at different spatial locations using a spatial array of monitoring points. Specifically, this includes: once the mixed wastewater has formed a stable water body in the main mixing zone, the pH monitoring action of the spatial array of monitoring points is activated, controlling all monitoring points to start collecting data at the same time. At fixed intervals, such as 2 seconds, each point simultaneously acquires the pH value of the mixed wastewater at its location. By using synchronous collection, pH data deviations caused by time differences in collection at different points are avoided, ensuring that the real-time pH readings of all points correspond to the water quality status of the main mixing zone at the same moment.

[0031] Step 2.3: Based on the values ​​of multiple real-time pH readings and their corresponding spatial relationships, calculate a dispersion index to characterize the pH distribution balance within the entire main mixing zone. Specifically, this includes: first, calculating the arithmetic mean of all real-time pH readings obtained from different spatial locations, using this as the basis for measuring the overall pH level of the main mixing zone; then, considering the spatial characteristics of each pH reading, such as points closer to and farther from the mixing device, or points in the upper and lower regions; analyzing the deviation of pH values ​​from the average value in different regions: generally, the farther a region is from the mixing device, the greater the deviation of its pH value from the average value, indicating a poorer mixing effect in that region; based on these deviations, by calculating the degree of deviation of all pH readings from the average value, obtain the dispersion index to characterize the pH distribution balance within the entire main mixing zone; the larger the dispersion index value, the more significant the pH difference at different locations within the main mixing zone, and the more uneven the water quality distribution; the smaller the value, the more concentrated the pH distribution in space, and the more ideal the mixing effect.

[0032] Step 2.4: Based on the dispersion index, dynamically adjust the weight allocation of the pH readings participating in the final calculation. By weighted fusion processing of multiple real-time pH readings, a current pH monitoring result that can represent the overall acid-base state of the mixed wastewater is obtained. Specifically, this includes: dynamically adjusting the weight allocation of each pH reading in the final fusion calculation based on the calculated dispersion index; when the dispersion index is small, such as less than or equal to 0.1, it indicates that the pH value distribution in the main mixing zone is uniform. At this time, the pH readings at all locations are similarly representative of the overall acid-base state, and each reading is assigned the same weight, and the current pH monitoring result is obtained by simple arithmetic average; when the dispersion index is large, such as greater than 0.1, it indicates that there is a local pH uneven distribution. At this time, a higher weight is assigned to the pH readings in areas that deviate more from the average value, and a lower weight is assigned to the pH readings in areas that deviate less from the average value, so as to highlight the water quality impact of areas with poor mixing effect; after completing the weight adjustment, each pH reading is multiplied by its corresponding weight, and then all products are summed to obtain the weighted fusion current pH monitoring result; this result comprehensively considers the pH distribution differences in different spatial locations and can more realistically reflect the overall acid-base state of the mixed wastewater.

[0033] In this embodiment of the invention, by arranging a spatial array of monitoring points consisting of multiple pH sensors inside the main mixing zone of the equalization tank, different spatial areas of the mixed wastewater within the main mixing zone can be covered, avoiding the limitation of traditional single-point monitoring that can only reflect local water quality. Based on the synchronous acquisition of multiple real-time pH readings at different locations using this spatial array, comprehensive spatial distribution data of pH values ​​within the main mixing zone can be obtained, providing sufficient basic information for judging water quality uniformity. By combining the values ​​of these pH readings with their corresponding spatial relationships to calculate the dispersion index, the distribution balance of pH values ​​within the entire main mixing zone can be intuitively quantified, clearly identifying areas with local acid-base imbalances. Then, the weight allocation of each pH reading is dynamically adjusted according to the dispersion index; the higher the dispersion, the higher the weight is assigned to pH readings in more dispersed areas. Through weighted fusion processing, the final current pH monitoring result can more accurately represent the overall acid-base state of the mixed wastewater, effectively avoiding monitoring deviations caused by local water quality unevenness. This provides a reliable parameter basis for dynamically adjusting the lime slurry dosage based on pH value and achieving precise neutralization treatment, helping to improve the stability and controllability of the entire neutralization reaction.

[0034] In a preferred embodiment of the present invention, step 3 above may include: Step 3.1: Based on the current pH monitoring results, and in conjunction with the preset target pH range, calculate the required theoretical dosage of lime slurry. Specifically, this includes: 1) Based on the current pH monitoring results, which integrate the pH distribution at different spatial locations in the main mixing zone and accurately reflect the overall acid-base state of the mixed wastewater; 2) Combining the preset target pH range, which is typically set to 7.0 to 8.0 for the neutralization requirements of gypsum-based acid wastewater. This range facilitates the formation of stable precipitates from fluoride and calcium ions while avoiding excessively high pH levels that could lead to lime slurry waste; 3) When calculating the required theoretical dosage of lime slurry, use the difference between the current pH monitoring results and the median of the target pH range as a basis, combined with the instantaneous treatment capacity of the mixed wastewater, where the instantaneous treatment capacity is determined by the sum of the transport rates of the three types of wastewater; 4) Referencing the effective neutralization concentration of the lime slurry, typically calculated as a 10% to 15% mass fraction, determine the total amount of lime slurry to be added per unit time to ensure that the pH of the mixed wastewater initially approaches the target range after addition.

[0035] Step 3.2: Based on the theoretical dosage of lime slurry, the lime slurry is injected into the neutralization reaction zone by adjusting the instantaneous flow rate. Specifically, this includes: first, converting the calculated theoretical dosage of lime slurry into the instantaneous flow rate of lime slurry per unit time, i.e., the volume of lime slurry to be injected into the neutralization reaction zone per minute or hour; based on the instantaneous flow rate, adjusting the delivery rate of the lime slurry injection pipeline to continuously and stably inject the lime slurry into the neutralization reaction zone; during injection, ensuring that the lime slurry injection position is near the inlet end of the neutralization reaction zone, so that the lime slurry can gradually participate in the reaction with the flow of mixed wastewater, avoiding uneven reaction caused by local accumulation of lime slurry.

[0036] Step 3.3: In the neutralization reaction zone, the lime slurry and mixed wastewater are brought into full contact and neutralized through stirring. Specifically, this includes: when the mixed wastewater flows out from the main mixing zone and enters the neutralization reaction zone along with the added lime slurry, the stirring operation in the reaction zone is started. The purpose of stirring is to promote rapid and uniform mixing of the lime slurry and the mixed wastewater. Through the water flow formed by stirring, the tiny droplets of lime slurry are dispersed into the mixed wastewater, breaking up the stratification that may form due to the density difference between the two, so that the hydroxide ions in the lime slurry can fully contact the hydrogen ions in the mixed wastewater and undergo a neutralization reaction. The stirring process continues, and the stirring intensity is controlled to form a gentle eddy current, which ensures the mixing effect and avoids water splashing or excessive energy consumption due to excessive stirring, until the mixed wastewater and lime slurry form a uniform reaction system.

[0037] Step 3.4: During the neutralization reaction, the instantaneous pH value of the effluent from the neutralization reaction zone is monitored in real time and compared with the target pH range. Specifically, this includes: real-time pH monitoring of the effluent from the neutralization reaction zone while the neutralization reaction continues, with the monitoring time interval consistent with the pH acquisition interval, such as once every 2 seconds, to ensure timely capture of the dynamic changes in the pH value of the wastewater after the reaction; the instantaneous pH value obtained from each monitoring is compared in real time with the preset target pH range of 7.0 to 8.0; if the instantaneous pH value is lower than 7.0, it indicates that the current lime slurry dosage is insufficient and the neutralization reaction is incomplete; if the instantaneous pH value is higher than 8.0, it indicates that the lime slurry dosage is excessive, which may lead to instability of the precipitation system; if the instantaneous pH value is between 7.0 and 8.0, it indicates that the current reaction state meets expectations.

[0038] Step 3.5: Based on the comparison results, perform closed-loop fine-tuning of the lime slurry dosage to ensure that the effluent pH value remains stable within the target pH range. Effluent with a stable pH value within the target pH range is defined as qualified neutralized wastewater. Specifically, this includes: performing closed-loop fine-tuning of the lime slurry dosage based on the comparison results; when the instantaneous pH value is lower than the lower limit of the target range, appropriately increasing the instantaneous flow rate of the lime slurry to increase the amount of lime slurry injected per unit time; when the instantaneous pH value is higher than the upper limit of the target range, appropriately decreasing the instantaneous flow rate to reduce the amount of lime slurry injected; when the instantaneous pH value is stable within the target range, maintaining the current flow rate unchanged; during the fine-tuning process, each adjustment should be controlled within 5% to 10% of the theoretical dosage to avoid drastic pH fluctuations due to large adjustments; through continuous closed-loop fine-tuning, ensure that the pH value of the effluent from the neutralization reaction zone remains stable within the target range of 7.0 to 8.0 for a long period, at which point the effluent is defined as qualified neutralized wastewater.

[0039] In this embodiment of the invention, the theoretical dosage of lime slurry is calculated based on the current pH monitoring results, which represent the overall acid-base state of the mixed wastewater, combined with a preset target pH range. This provides a precise water quality basis for the dosage calculation, avoiding the blindness of traditional methods that rely solely on experience or single data points. The instantaneous flow rate of lime slurry is adjusted according to this theoretical dosage and injected into the neutralization reaction zone to ensure that the lime slurry enters the reaction system stably in the required amount, providing a material basis for the orderly conduct of the neutralization reaction. Stirring within the neutralization reaction zone promotes full contact between the lime slurry and the mixed wastewater, eliminating potential issues of insufficient contact and resulting in a more uniform and complete neutralization reaction, reducing localized incomplete reactions. Real-time monitoring of the instantaneous pH value of the effluent from the neutralization reaction zone during the reaction process, compared with the target range, allows for timely capture of pH value changes and monitoring of the real-time reaction status. Closed-loop fine-tuning of the lime slurry dosage is then performed based on the comparison results, specifically correcting dosage deviations and avoiding pH fluctuations caused by traditional static control. This ensures that the effluent pH value remains stable within the target range, ultimately yielding qualified neutralized wastewater. This series of steps are interconnected, from calculating the dosage to controlling the reaction process and correcting the results, forming a complete neutralization control process that effectively overcomes the problem of the crude control of traditional neutralization reactions.

[0040] In a preferred embodiment of the present invention, step 4 above may include: Step 4.1 involves guiding the qualified neutralized wastewater through a pre-designed delivery pipeline. Specifically, this includes introducing the qualified neutralized wastewater into the pre-designed delivery pipeline. During pipeline construction, sharp bends and abrupt changes in inner diameter should be avoided, as sharp bends easily generate localized eddies, and abrupt changes in inner diameter lead to sudden changes in water flow velocity. Both of these can cause irregular concentration distribution of the wastewater within the pipeline, affecting the representativeness of the test data. After the wastewater enters the pipeline, the flow pattern is determined by observing the water flow state in the transparent observation section of the pipeline: if the streamlines are parallel and there is no significant disturbance, it indicates a stable laminar or slow flow state; if the streamlines are turbulent and vortices appear, the water flow velocity needs to be gradually adjusted to 1.0 to 1.5 m / s by adjusting the valve opening at the front end of the pipeline until the flow pattern stabilizes. Maintaining this flow velocity aims to ensure that the dissolved calcium ions, fluoride ions, and pH value in the water remain relatively uniform during the delivery process, avoiding uneven ion distribution due to excessively high flow rates or particle sedimentation due to excessively slow flow rates, thus providing a stable water quality basis for establishing a test section at the pipeline outlet.

[0041] Step 4.2: At the outlet of the delivery pipeline, establish a detection section perpendicular to the wastewater flow direction. Specifically, this includes: selecting a location 5 to 10 cm from the edge of the outlet as the installation point for the detection section; this location is far from the water diffusion zone at the outlet edge, as the water flow at the edge is easily affected by the outside air and the parameters are unstable, and it can directly reflect the true state of the wastewater before it enters the sedimentation tank; when establishing the detection section, first mark a baseline on the outer wall of the pipeline along the water flow direction, then attach a flat metal plate as the section carrier to the outlet end face of the pipeline, and use a level to calibrate the angle between the plate and the baseline: if the bubble in the level is centered, it means that the plate is perpendicular to the water flow direction, and the angle is 90°; if the bubble is off-center, fine-tune the angle of the plate until it is perpendicular; at the same time, use a ruler to slide along the surface of the plate to check to ensure that there are no protrusions or depressions on the plate surface, to avoid water stagnation at the section due to uneven carrier, which would interfere with the distribution of water quality parameters, and to build a regular spatial reference surface for accurately calibrating the sampling point.

[0042] Step 4.3: On the inspection section, accurately mark the center position of the pipe, the upper position at one-quarter radius from the pipe wall, and the lower position at one-quarter radius from the pipe wall as three specific spatial points. This includes: First, using a measuring tape to encircle the outer wall of the pipe and measure its circumference. Calculate the inner diameter and radius from the circumference, where the radius equals the circumference divided by 2π. Next, use the cross-sectional method to locate the center of the pipe cross-section: Mark four points evenly along the circumference on the outer wall of the pipe. Connect opposite points with a measuring tape to form two perpendicular lines, representing the two diameters of the pipe. The intersection of these two lines is the center of the circle. The projection of this center onto the inspection section is the center position of the pipe. Using the center as... The origin is marked by measuring one-quarter of the radius upwards with a ruler along a direction perpendicular to the horizontal axis of the pipe, i.e., the vertical direction. Then, measuring one-quarter of the radius downwards is marked as another point. These two points are located at the upper and lower sides of the pipe wall, respectively, representing the distance from the pipe wall to the upper and lower sides. The logic for selecting these three points is as follows: there is a sidewall effect in the water flow within the pipe, with the water flow being fastest and ion mixing being most thorough at the center; the water flow is slowest at the sidewalls, making it prone to local ion accumulation; the one-quarter radius is a transitional region between flow velocity and ion concentration, and the two points above and below can cover the vertical concentration difference. Combining these three points can comprehensively capture the water quality gradient within the cross-section, avoiding the limitation of a single point only reflecting the local state.

[0043] Step 4.4: Set the three specific spatial locations as fixed sampling points; using a multi-parameter water quality sensor, synchronously collect the pH value, calcium ion concentration, and fluoride ion concentration at the three sampling points within a set time window. Specifically, this includes: marking the three points as fixed sampling points on the detection cross-section carrier with an erasable marker, ensuring the markings are flush with the carrier surface to avoid protrusions interfering with water flow; selecting a multi-parameter water quality sensor with simultaneous pH, calcium ion, and fluoride ion detection functions, and calibrating the sensor in advance to ensure that the detection errors of the three parameters are controlled within the allowable range; setting a 10-second sampling interval. The time window is set up by aligning the three independent detection probes of the sensor with the three sampling positions using an adjustable bracket. The probe depth is adjusted to be flush with the inner wall of the pipe to avoid being inserted too deeply or too shallowly. The synchronous triggering function of the sensor controls the three probes to contact the wastewater and start detection at the same time. Synchronous acquisition can eliminate errors caused by time difference. For example, if the center point is collected first and then the side wall point is collected, the water flow may carry ions, resulting in data mismatch. During the acquisition process, the bracket is kept stable to prevent the probes from shifting the sampling position due to the impact of water flow, ensuring that the three parameters of each point correspond to the water state at the same time.

[0044] Step 4.5: Summarize the synchronously collected pH, calcium ion concentration, and fluoride ion concentration into three key water quality parameters. Specifically, this includes: categorizing and organizing the synchronously collected raw data according to parameter type and sampling location: First, list the pH data from the three sampling locations separately, labeling the location of each data point, such as the center, upper quarter radius, and lower quarter radius; then organize the calcium ion concentration data and fluoride ion concentration data in the same way, forming three independent sets of location-value correspondence tables. During this process, pay attention to any significant outliers in a particular set of data, such as those appearing in contrast to the other two sets. If the numerical difference at a point exceeds 20%, the abnormal location needs to be recorded, but it will not be removed immediately because the abnormal value may reflect the true concentration gradient at that point and needs to be analyzed in the next step of the correction process. The reason why these three parameters are identified as key water quality parameters is that pH value determines the dissolution balance of CaF2 and Ca3(PO4)2 precipitates in the sedimentation tank, and the concentration ratio of calcium ions to fluoride ions directly affects the precipitation rate and particle size. The three together constitute the core indicators for judging the sedimentation potential of wastewater. The summarized parameter set will serve as the original basis for constructing the virtual space configuration and calculating the comprehensive correction value.

[0045] In this embodiment of the invention, qualified neutralized wastewater is first fed through a pre-set delivery pipeline to ensure that the wastewater flows stably towards the sedimentation tank along a predetermined path, providing a stable water flow basis for water quality testing. A detection section is established perpendicular to the water flow direction at the outlet of the delivery pipeline, creating a reasonable spatial plane for accurately calibrating the sampling location. Three spatial points are precisely calibrated on the detection section: the center of the pipeline, the upper side at a quarter radius from the pipe wall, and the lower side. These points cover different areas of the pipeline section, reflecting the possible concentration gradient differences of the wastewater within the pipeline, avoiding the limitations of traditional single-point sampling which only represents local water quality. Limitations: After setting three sampling points as fixed sampling locations, the pH value, calcium ion concentration, and fluoride ion concentration of each point were collected synchronously within a set time window. Synchronous collection ensured the correspondence of the three parameters at the same time point, avoiding data deviation caused by time difference. Finally, the synchronously collected parameters were summarized into three key water quality parameters. These parameters comprehensively and accurately reflect the overall water quality status of the neutralized wastewater before it enters the sedimentation tank, providing reliable raw data support for constructing virtual space configuration, performing joint parameter correction, and predicting sedimentation trends in subsequent steps, effectively improving the control accuracy of the treatment process.

[0046] In a preferred embodiment of the present invention, step 5 above may include: Step 5.1: Obtain the spatial location information of the three sampling points and the corresponding three key water quality parameters. Specifically, this includes: extracting detailed information for each of the three sampling points from the compiled parameter data; for the spatial location information, measuring and recording the distance between each sampling point and the inner wall of the pipe, the straight-line distance between the three points (e.g., the vertical distance from the center to the upper quarter-radius point, the vertical distance from the center to the lower quarter-radius point), and their relative orientation on the detection cross-section to clarify the positional relationship between the upper, lower, and center points; for the three key water quality parameters, recording the specific parameters for each sampling point. The data includes numerical values, such as pH 7.2, calcium ion concentration 120 mg / L, and fluoride ion concentration 80 mg / L at the center point; pH 7.1, calcium ion concentration 110 mg / L, and fluoride ion concentration 75 mg / L at the upper point; and pH 7.3, calcium ion concentration 125 mg / L, and fluoride ion concentration 85 mg / L at the lower point. This information is then compiled into a table, with the sampling location name in the left column, the spatial location characteristics in the middle column, and the corresponding three parameter values ​​in the right column, forming a complete dataset that links spatial location with water quality data.

[0047] Step 5.2: Based on the spatial location information of the three sampling points, construct a virtual reference plane; map the key water quality parameters corresponding to the sampling points located at the center of the pipeline to a theoretical projection point on the virtual reference plane. Specifically, this includes: establishing a two-dimensional coordinate system based on the recorded spatial relationship of the three sampling points, with the center point of the detection section as the origin; marking the coordinates of the upper quarter radius point, the lower quarter radius point, and the center point as (0, r / 4), (0, -r / 4), and (0, 0), respectively, where r is the pipeline radius; based on the coordinates of these three points, using the principle of three points determining a plane in plane geometry, construct a virtual reference plane that completely coincides with the detection section; this plane simulates the actual distribution of wastewater at the pipeline outlet. The spatial arrangement of the three sampling points can be visually presented. Next, assuming that the water quality in the pipe is ideally uniform, i.e., there is no concentration gradient, the theoretical parameters of the center point should be consistent with the parameters of the upper and lower points. The average of the three parameters of the upper and lower points is taken as the theoretical value under ideal conditions. For example, the theoretical pH value is 7.1 plus 7.3 divided by 2 equals 7.2, the theoretical calcium ion concentration is 110 plus 125 divided by 2 equals 117.5 mg / L, and the theoretical fluoride ion concentration is 75 plus 85 divided by 2 equals 80 mg / L. This set of theoretical values ​​is mapped to the center coordinates 0,0 of the virtual reference plane to form a theoretical projection point. This point represents the parameter state that the center position should have when the water quality is uniform, providing a clear reference standard for comparing actual parameters.

[0048] Step 5.3: Calculate the overall deviation between the actual key water quality parameters at the central sampling point and the theoretical projection point; based on the overall deviation, form a comprehensive correction value, specifically including: first, calculating the individual deviation values ​​of the actual parameters at the central point and the parameters at the theoretical projection point: subtract the values ​​of the corresponding parameters at the theoretical projection point from the actual pH value, calcium ion concentration, and fluoride ion concentration at the central point to obtain the deviation values ​​of each of the three parameters, where a positive value indicates that the actual value is higher than the theoretical value, and a negative value indicates that the actual value is lower than the theoretical value: pH value deviation is actual 7.2 minus theoretical 7.2 equals 0, calcium ion concentration deviation is 120 minus 117.5 equals 2.5 mg / L, and fluoride ion concentration deviation is 80 minus 80 equals 0; combined with gypsum In the treatment of acid wastewater, the influence of various parameters is as follows: fluoride ion concentration directly determines the amount of CaF2 precipitate formed and has the greatest impact on the precipitation effect; pH value affects the equilibrium direction of the precipitation reaction; calcium ion concentration provides reaction raw materials for precipitation. Different weights are assigned to the three deviation values, with fluoride ion deviation weight set at 40%, pH value deviation weight set at 30%, and calcium ion deviation weight set at 30%. The absolute value of each deviation value is multiplied by its corresponding weight and then summed to obtain the comprehensive deviation degree of 0.75. Based on the magnitude and direction of the comprehensive deviation degree, a positive value indicates that the actual value is higher than the theoretical value, forming a comprehensive correction value of -0.75, while a negative sign indicates that the actual value needs to be adjusted down to the theoretical value. This value quantifies the deviation of the central point parameter from the ideal state.

[0049] The core basis for determining the weighting of the three parameters—fluoride ions (40%), pH (30%), and calcium ions (30%)—is as follows: The core pollutant in gypsum-based acid production wastewater is fluoride ions. Flue gas scrubbing wastewater contains fluoride ions due to the absorption of acidic components from kiln gas, and the national emission limits for fluorides are strictly controlled. At the same time, the concentration of fluoride ions directly determines the amount and stability of CaF2 precipitate in the sedimentation tank. Deviations in fluoride ion concentration will directly lead to significant fluctuations in the CaF2 precipitate formation rate and particle size, thereby affecting the sedimentation effect. It is a key indicator that determines whether the wastewater can ultimately meet the discharge standards or be reused. Therefore, it is given the highest weight, i.e., the weight of fluoride ions is set at 40%.

[0050] The target pH value needs to be stable within the range of 7.0 to 8.0. This range is a key factor affecting the precipitation and dissolution equilibrium of CaF2 and Ca3(PO4)2, because deviations from the target pH value will lead to insufficient precipitation dissolution or formation. For example, when the pH is below 7.0, the solubility of CaF2 increases, and when the pH is above 8.0, calcium hydroxide flocs are easily formed, interfering with sedimentation. However, the influence of pH value can be quickly corrected by adjusting the amount of lime slurry added, and its deviation has a weaker direct effect on the precipitation effect than fluoride ions. Therefore, its weight is lower than that of fluoride ions, i.e., the pH value weight is set at 30%. Calcium ions are the reaction raw materials for the precipitation of CaF2 and Ca3(PO4)2, and their concentration deviation will affect the precipitation formation efficiency. However, the calcium ions in gypsum acid production wastewater mainly come from raw material residues carried by surface flushing wastewater, and their content is relatively stable. Even if there is a deviation in the calcium ion concentration, it can be compensated for by adjusting the influent rate of the subsequent sedimentation tank (extending the residence time) or by supplementing a small amount of calcium source. The degree of influence on the final precipitation effect is similar to that of pH value, so it is given the same weight as pH value, i.e., the calcium ion weight is set at 30%.

[0051] When calculating the overall deviation, the absolute values ​​of the individual deviations of the three parameters are multiplied by their corresponding weights: fluoride ions × 40%, pH value × 30%, and calcium ions × 30%. These products are then summed to obtain the overall deviation, which characterizes the difference between the actual parameters at the center point and the ideal state. When generating the overall correction value, the value is determined based on the numerical value and sign of the overall deviation. If the overall deviation is positive, it indicates that the actual parameters at the center point are generally higher than the theoretical value; the overall correction value is a negative value equal to the overall deviation, used to adjust the actual value downwards towards the theoretical value. If the overall deviation is negative, it indicates that the actual parameters at the center point are generally lower than the theoretical value; the overall correction value is a positive value equal to the overall deviation, used to adjust the actual value upwards towards the theoretical value. This ensures that the correction direction is opposite to the parameter deviation direction and that the correction magnitude matches the overall deviation.

[0052] Step 5.4: Based on the comprehensive correction value, perform joint correction processing on the original key water quality parameters simultaneously obtained from the three sampling locations. Specifically, this includes: performing joint correction on the original parameters of the three sampling locations based on the obtained comprehensive correction value minus 0.75. Two principles must be considered during correction: first, maintain a reasonable concentration gradient across the pipe cross-section, as there should be slight differences between the edge and center parameters due to the sidewall effect; second, maintain the chemical balance among the three parameters, such as the pH value and the dissolution balance of calcium and fluoride ions. In specific operation, first adjust the calcium ion concentration at the center point proportionally, reducing it by 2.5 mg / L from 120 mg / L to 117.5 mg / L, which is closer to the theoretical value. To ensure the correct values ​​are corrected, and considering the gradient correlation between the upper and lower points and the center, the calcium ion concentration on the upper side was increased by 1.25 mg / L to 111.25 mg / L, and the calcium ion concentration on the lower side was decreased by 1.25 mg / L to 123.75 mg / L, so that the three values ​​still maintain a reasonable vertical gradient. For pH and fluoride ion concentration, since the deviation value of each is 0, the original values ​​are kept unchanged. However, it is necessary to check whether the adjusted calcium ion concentration matches the pH value. For example, at pH 7.2, is the calcium ion concentration of 117.5 mg / L within a stable range? This ensures that the three parameters still conform to the chemical equilibrium law after correction, and avoids system imbalance caused by adjusting a single parameter.

[0053] Step 5.5: Through joint correction processing, a set of corrected parameters that more accurately reflect the overall properties of the water body is obtained. Specifically, after joint correction, a new set of parameter data is obtained: At the central point, pH 7.2, calcium ion 117.5 mg / L, and fluoride ion 80 mg / L; at the upper point, pH 7.1, calcium ion 111.25 mg / L, and fluoride ion 75 mg / L; at the lower point, pH 7.3, calcium ion 123.75 mg / L, and fluoride ion 85 mg / L. The characteristic of this set of corrected parameters is that it corrects the abnormally high calcium ion concentration at the central point. This method eliminates biases caused by sampling or uneven distribution while preserving the natural concentration gradient between the upper, lower, and center sides, conforming to the actual distribution pattern of water flow in the pipeline. Furthermore, the proportional relationship between the three parameters better matches the chemical equilibrium conditions of the CaF2 precipitation reaction, such as the calcium ion to fluoride ion concentration ratio being within a reasonable range. By comparing the data before and after correction, it can be seen that the corrected parameters more accurately reflect the overall water quality state of the wastewater before it enters the sedimentation tank, solving the problem of representative distortion that may be caused by local disturbances in the original data. This provides a more accurate and reliable basis for analyzing the formation and settling trends of sediments.

[0054] In this embodiment of the invention, by acquiring the spatial location information of three sampling positions and the corresponding three key water quality parameters, complete basic information including spatial location and water quality data is provided for parameter calibration, ensuring that the calibration process has a clear original basis. A virtual reference plane is constructed based on the spatial location information of the three sampling positions, and the key water quality parameters of the central sampling position are mapped to theoretical projection points, establishing a correlation between water quality parameters and spatial location, providing a virtual reference standard for judging whether the actual parameters deviate from the ideal distribution. The comprehensive deviation between the actual key water quality parameters at the central location and the theoretical projection points is calculated and a comprehensive correction value is formed, accurately quantifying the original... The deviations caused by spatial distribution differences in parameters avoid the subjectivity of judging deviations based on experience. The original key water quality parameters of the three sampling locations are jointly corrected based on the comprehensive correction value, breaking the limitations of independent correction of a single parameter. This makes the correction process take into account the mutual influence between parameters and the spatial distribution law. Finally, the corrected parameters that can more accurately reflect the overall properties of the water body are obtained through joint correction. This effectively solves the problem of insufficient local representativeness of the original sampling data. It provides accurate and reliable data support for predicting the sedimentation state and sedimentation trend in the sedimentation tank based on parameters, and improves the scientificity and accuracy of subsequent sedimentation process control.

[0055] In a preferred embodiment of the present invention, step 6 above may include: Step 6.1 involves comparing and analyzing the corrected parameters with the preset empirical thresholds for precipitate formation and settling. Specifically, this includes: first, defining the preset empirical thresholds for precipitate formation and settling. These thresholds are based on long-term laboratory tests and field operation data for gypsum-based acid wastewater treatment, and are set according to the characteristics of the main precipitates CaF2 and Ca3(PO4)2 in the sedimentation tank; for example, the pH threshold range is 7.0 to 8.0, within which the solubility of both precipitates is lowest, resulting in the most stable formation; the calcium ion to fluoride ion concentration ratio threshold is 1.2 to 1.5, at which the CaF2 precipitation rate and particle size distribution are optimal. The water quality is of moderate size, which facilitates sedimentation. Simultaneously, a single ion concentration threshold is set, such as a fluoride ion concentration not exceeding 100 mg / L, to prevent excessively fine sediment particles from affecting sedimentation. The corrected parameters obtained, namely the pH value, calcium ion concentration, fluoride ion concentration, and their ratio at the three sampling points, are compared item by item with these empirical thresholds. First, it is determined whether the pH value is within 7.0 to 8.0; then, the calcium ion to fluoride ion concentration ratio is checked to be between 1.2 and 1.5; finally, it is confirmed whether the single ion concentration does not exceed the upper limit. Through multi-dimensional comparison, the difference between the current water quality parameters and the ideal sedimentation conditions is clarified.

[0056] The detailed process and basis for developing long-term laboratory test and field operation data are as follows: Laboratory test data: Using actual wastewater from a phosphogypsum-based acid production project as a sample, multiple parallel experiments were conducted to control a single variable and test the effect of different parameters on precipitation. (The last part, "Ca," appears to be incomplete and lacks context. It's unclear what "Ca" refers to.) 2+ With F - Under constant concentration conditions, the effects of different pH ranges on the solubility and precipitate particle size of CaF2 were tested. The results showed that the solubility of CaF2 was lowest and the precipitate particle size was conducive to sedimentation when the pH was between 7.0 and 8.0. Under constant pH conditions, the effects of different CaF2 concentrations on the solubility and precipitate particle size were tested. 2+ With F - The effect of concentration ratio on the formation rate and sedimentation velocity of CaF2 was investigated. Results showed that when the concentration ratio was between 1.2 and 1.5, the formation rate was stable and the sedimentation velocity was good. Under conditions where pH and concentration ratio were constant, different F... - The effect of concentration on precipitation effect, the results show F - When the concentration does not exceed 100 mg / L, the effluent after sedimentation easily meets the standards. Based on these results, the threshold ranges for each parameter were preliminarily determined.

[0057] On-site operational data: Long-term operational results were continuously recorded in the wastewater treatment systems of multiple gypsum-based acid production lines. When the pH was between 7.0 and 8.0, and the Ca... 2+ With F - The concentration ratio is between 1.2 and 1.5, F - When the concentration does not exceed 100 mg / L, the effluent compliance rate of the sedimentation tank remains stable at a high level, and the sludge disposal is relatively easy. When the parameters deviate from this range, the effluent compliance rate drops significantly. Based on this, the field applicability of the laboratory threshold was verified, and the empirical threshold system was finally determined.

[0058] Method for comparing the corrected parameters with the threshold: The pH value, Ca2+ value, and Ca2+ value obtained from the three sampling points after correction are compared. 2+ Concentration, F - Concentrations were compared item by item according to the following dimensions: First, pH value comparison, determining whether the pH values ​​of the three sampling points were all within the range of 7.0 to 8.0, and whether the differences between the values ​​at each point were small; second, concentration comparison, calculating the Ca at each sampling point. 2+ With F - The concentration ratio was checked to determine if it was all within the range of 1.2 to 1.5; thirdly, F... - Concentration comparison to determine the F value at three sampling points. - Whether the concentration does not exceed 100 mg / L. By comparing multiple dimensions, the differences between the current water quality parameters and the ideal sedimentation conditions are clarified, providing a basis for predicting the sedimentation rate.

[0059] Step 6.2: Based on the comparative analysis results, predict the formation rate and settling velocity of sediment in the sedimentation tank under the current water quality conditions. Specifically, this includes: predicting the rate based on the comparative analysis results and the basic laws of sediment formation and settling; if the corrected pH value is between 7.5 and 8.0, the calcium ion to fluoride ion concentration ratio is between 1.3 and 1.4, and the concentration of any single ion does not exceed the standard, it indicates that the current water quality is close to ideal conditions. It is predicted that the formation rate of CaF2 and Ca3(PO4)2 will be stable, the sediment particle size will be relatively large (approximately 50 to 100 μm), and the settling velocity will be relatively fast (approximately 0.5 to 0.8 μm). If the pH value is below 7.0 and the calcium ion to fluoride ion concentration ratio is less than 1.2, it indicates that the precipitation reaction is insufficient, the predicted formation rate is slow, and the particles are fine (less than 30 μm), with a settling velocity below 0.3 m / h. If the fluoride ion concentration exceeds 100 mg / L, even if the ratio is within the threshold, the predicted formation rate is too fast, the precipitated particles are too fine (less than 20 μm), and the settling velocity drops below 0.2 m / h. The entire prediction process is based on the degree of deviation between the parameters and the threshold. The greater the deviation, the smaller the predicted deviation range of the rate, ensuring that the prediction results are consistent with the actual water quality conditions.

[0060] Step 6.3: Based on the predicted generation rate and settling velocity, determine whether the operating conditions of the sedimentation tank need to be adjusted. Specifically, this includes: quantitatively comparing the predicted sediment generation rate and settling velocity to determine their balance; when the ratio of generation rate to settling velocity is between 0.8 and 1.2, it indicates that the amount of sediment generated and the amount of sediment settled are basically matched, and there will be no sediment accumulation or overflow of unsettled particles in the sedimentation tank, so no adjustment of operating conditions is needed; when the ratio is greater than 1.2, it means that the generation rate exceeds the settling velocity. If the current operation is maintained, sediment accumulation at the bottom of the sedimentation tank and an increase in suspended solids in the upper water body will occur in the short term, eventually leading to effluent exceeding the standard, and the operating conditions need to be adjusted; when the ratio is less than 0.8, the generation rate is too slow. Although it will not cause effluent problems, it will waste the sedimentation tank volume. It can be decided whether to make minor adjustments based on production needs, such as increasing the influent rate to increase the treatment capacity. The core judgment criteria revolve around whether it affects the stability of effluent water quality to ensure that the adjustment decision is targeted.

[0061] Step 6.4: When the predicted settling velocity is lower than the generation rate, reduce the influent rate of the sedimentation tank or initiate the flocculant addition process. Specifically, when the ratio of the generation rate to the settling velocity is determined to be greater than 1.2, i.e., the settling velocity is lower than the generation rate, reduce the influent rate of the sedimentation tank or initiate the flocculant addition process. When reducing the influent rate, adjust according to the degree of deviation of the ratio. If the ratio is between 1.2 and 1.5, reduce the influent rate by 10% to 20%, thereby extending the residence time of wastewater in the sedimentation tank from the original 2 hours to 2.2 to 2.4 hours, resulting in fine sediment particles. Provide more sufficient settling time; if the ratio exceeds 1.5, simply reducing the influent rate is not enough to improve the situation quickly, and the flocculant addition process must be started simultaneously. Polyaluminum chloride is selected as the flocculant, which can agglomerate fine CaF2 and Ca3(PO4)2 particles into large flocs through adsorption bridging, increasing the particle size from 20μm to over 80μm, thereby accelerating the settling speed. The dosage is determined according to the corrected fluoride ion concentration. For every 10mg / L increase in concentration, the dosage of polyaluminum chloride is adjusted by increasing it by 5mg per liter of wastewater to ensure accurate and effective addition of the flocculant.

[0062] Step 6.5 involves optimizing the properties of the wastewater to be treated by adjusting the influent rate or adding flocculant, resulting in optimized sedimentation influent. Specifically, this includes: after the adjustment operation, the properties of the wastewater are gradually optimized; by reducing the influent rate, the hydraulic residence time of the wastewater in the sedimentation tank is extended, allowing fine particles that were previously unable to settle due to excessive flow velocity to have more time to settle downwards under gravity, thus reducing the initial concentration of suspended particles in the water; and after initiating the flocculant addition process, polyaluminum chloride is thoroughly mixed with the wastewater. The polynuclear hydroxy complexes produced by hydrolysis are adsorbed on the surface of the precipitated particles, causing the particles to attract and collide with each other, forming large flocs with a compact structure. The settling speed of the flocs is 3 to 5 times higher than that of the original particles. Through these two operations, the settling performance of the wastewater to be treated is significantly improved. The proportion of settling particles in the water increases from 60% before adjustment to more than 85%, and the average particle size increases from 30μm to more than 60μm. Finally, a precipitated influent with optimized properties is formed. After entering the sedimentation tank, this influent is more suitable for the settling conditions of the sedimentation tank.

[0063] In this embodiment of the invention, the corrected parameters are compared and analyzed with preset empirical thresholds for sediment formation and settling. This provides a clear reference standard for determining whether the current water quality is conducive to the sedimentation reaction, avoiding the subjectivity of traditional processes that rely on experience. Based on the comparison results, the formation rate and settling velocity of sediment in the sedimentation tank are predicted, enabling proactive control of the sedimentation process and overcoming the shortcomings of traditional processes that cannot detect the sedimentation state in advance and can only passively respond to excessive effluent. The determination of whether to adjust the operating conditions of the sedimentation tank based on the predicted rate relationship makes subsequent regulation more targeted and avoids resource waste caused by blind adjustments. If the treatment is inefficient or the treatment effect is poor, when the predicted settling rate is lower than the generation rate, the influent rate should be reduced in time or the flocculant addition process should be started to actively optimize the sedimentation conditions and prevent the effluent suspended solids from exceeding the standard due to the excessively rapid formation of precipitates and the untimely settling. By optimizing the properties of the wastewater to be treated through these operations, the resulting optimized sedimentation influent can make the sedimentation reaction in the sedimentation tank more complete and the settling smoother, effectively improving the sedimentation efficiency and effect, providing a guarantee for obtaining clear liquid that meets the standards, and reducing the treatment pressure caused by unstable sedimentation effect, thus helping to improve the stability of the entire wastewater treatment process and the resource recovery rate.

[0064] In a preferred embodiment of the present invention, step 7 above may include: Step 7.1: Introduce the optimized sedimentation influent into the uniform water distribution zone of the sedimentation tank. Within the sedimentation tank, suspended solids and the generated CaF2 and Ca3(PO4)2 precipitates are naturally separated by gravity. Specifically, the optimized sedimentation influent is introduced into the uniform water distribution zone of the sedimentation tank through a pipe. The distribution zone is equipped with a perforated water distribution plate. As the water flows through the holes of the distribution plate, it is dispersed into multiple fine streams, flowing evenly to the main area of ​​the sedimentation tank, preventing excessively rapid local water flow from impacting the sediment at the bottom or causing water disturbance. After entering the sedimentation tank, gravity is used to facilitate the separation of suspended solids and generated CaF2 in the water. Ca3(PO4)2 settles naturally; larger particles, due to gravity exceeding the buoyancy of water, sink rapidly after entering the sedimentation tank, gradually accumulating at the bottom to form a sludge layer; smaller flocs, formed after treatment with flocculants, collide with each other during slow flow, further agglomerating into larger particles, which gradually settle as the water flows; throughout the process, the depth of the sedimentation tank is typically designed to be 4 to 5 meters, matching the water flow velocity, which is controlled at 0.005 to 0.01 m / s, providing sufficient settling path and time for particles of different sizes, ensuring that most suspended solids and sediments can be separated from the water.

[0065] Step 7.2: After the set settling time is reached, collect effluent samples from the upper clear water zone of the sedimentation tank and monitor the turbidity and key ion concentrations of the effluent samples. Specifically, this includes: setting a corresponding settling time based on the adjusted hydraulic retention time, such as extending it to 2.2 to 2.4 hours; starting to collect effluent samples after the sedimentation influent has remained in the sedimentation tank for the full settling time; selecting the sampling point in the upper clear water zone of the sedimentation tank, 30 to 50 cm above the water surface, where the water has completed settling, the suspended solids content is the lowest, and interference from floating objects is avoided; during sampling, a special sampler is slowly inserted into the water to avoid disturbing the particles that have not fully settled below, and three parallel samples are collected each time to reduce errors; during monitoring, turbidity is directly read using a turbidimeter, reflecting the amount of remaining suspended solids in the water; key ion concentrations, fluoride ions and calcium ions, are measured using the ion-selective electrode method, where the fluoride ion concentration directly relates to whether the discharge meets the standards, and the calcium ion concentration affects the scaling risk to production equipment during reuse, and all monitoring data are recorded in real time.

[0066] Step 7.3 involves comparing and verifying the monitoring results against preset emission or reuse standards. Specifically, the preset emission or reuse standards are formulated based on the environmental protection requirements and production needs of the gypsum-based acid production industry. The emission standards require a fluoride ion concentration of less than or equal to 10 mg / L and a turbidity of less than or equal to 5 NTU. The reuse standards, used for flue gas scrubbing, require a fluoride ion concentration of less than or equal to 5 mg / L, a turbidity of less than or equal to 3 NTU, and a calcium ion concentration of less than or equal to 80 mg / L to prevent scaling on the scrubbing equipment. The monitoring results are compared item by item with these standards. First, check whether the turbidity meets the corresponding standard, then verify whether the fluoride ion concentration meets the standard. If used for reuse, it is also necessary to confirm whether the calcium ion concentration is within the limit. During the comparison, not only should individual parameters be considered as qualified, but a comprehensive judgment is also required. For example, if the turbidity meets the standard but the fluoride ion concentration exceeds the standard, it is still considered as not meeting the standard, to ensure that the treated clear liquid meets the requirements in all indicators.

[0067] Step 7.4: When the verified monitoring results meet the standards, the qualified clear liquid is collected for direct discharge or reuse in the production process. Specifically, when the comparison results show that all monitoring parameters meet the preset standards, the clear water discharge valve at the top of the sedimentation tank is opened, and the qualified clear liquid is introduced into the collection tank through a dedicated pipeline. During the collection process, the water flow is kept stable to avoid stirring the sediment at the bottom of the tank, which would cause secondary pollution of the clear liquid. If it is used for direct discharge, the collected clear liquid is metered by the final flow meter and discharged into the main sewage treatment network of the plant through the discharge port to ensure that the discharge volume meets the limit approved by the environmental protection department. If it is used for reuse in the production process, the clear liquid is pumped to the storage tank of the flue gas scrubbing process and mixed with fresh water in a certain proportion before use. The reuse rate can usually reach 60% to 70%, which reduces the consumption of fresh water and the cost of deep treatment, and realizes the recycling of water resources.

[0068] Step 7.5: When the verified monitoring results do not meet the standards, a portion of the clarified liquid is returned to the equalization tank for further treatment. Specifically, when the comparison results show that the monitoring parameters do not meet the standards, such as a fluoride ion concentration of 12 mg / L exceeding the emission limit, or a turbidity of 6 NTU exceeding the reuse standard, the clarified water discharge valve is closed, the return pipeline valve is opened, and a portion of the clarified liquid is returned. The return ratio is determined according to the degree of exceedance: 30% to 40% for slight exceedances and 50% to 60% for severe exceedances. The returned clarified liquid is then pumped to the equalization tank. The returned clarified liquid is remixed with the original wastewater in the equalization tank and undergoes pH monitoring, neutralization reaction, and other treatment processes again. Through secondary adjustment and reaction, the concentration of suspended solids and ions in the water is reduced until the subsequent treatment meets the standards. This return and retreatment mechanism forms a closed loop, avoiding the environmental risks caused by the direct discharge of substandard wastewater. At the same time, the water quality is gradually optimized through repeated treatment, ensuring the stable operation of the entire process.

[0069] In this embodiment of the invention, optimized influent is introduced into the uniformly distributed water zone of the sedimentation tank. Combined with gravity, suspended solids and CaF2 and Ca3(PO4)2 precipitates are naturally separated through sedimentation. This fully utilizes the excellent settling properties of the optimized influent, reduces hydraulic disturbance within the sedimentation tank, and improves the efficiency and thoroughness of sedimentation separation. After the set set settling time, effluent samples are collected from the upper clear water zone to monitor turbidity and key ion concentrations. This accurately reflects the actual treatment effect of the sedimentation tank and avoids detection deviations caused by improper sampling locations. The monitoring results are compared and verified with preset discharge or reuse standards, providing a basis for the disposal of the clarified liquid. Clear criteria are established to ensure that the treated water quality meets environmental or production requirements. When monitoring results meet the standards, the clarified liquid is collected for direct discharge or reuse in production, which not only meets environmental emission limits but also improves the wastewater resource reuse rate and reduces fresh water consumption and deep treatment costs. When monitoring results fail to meet the standards, part of the clarified liquid is returned to the equalization tank for further treatment, forming a closed-loop control process of treatment, monitoring, return, and retreatment. This avoids the environmental risks of direct discharge of substandard wastewater and further optimizes water quality through retreatment, ensuring the stability and reliability of the entire wastewater treatment process and helping the gypsum acid production industry achieve clean production and efficient resource recycling.

[0070] like Figure 2 As shown, embodiments of the present invention also provide a wastewater treatment and control system for clean production of gypsum-based acid, comprising: The monitoring module is used to mix flue gas scrubbing wastewater, equipment cooling wastewater and floor flushing wastewater in an equalization tank to form mixed wastewater; and to monitor the pH value of the mixed wastewater in real time to obtain the current pH monitoring results. The adjustment module dynamically adjusts the amount of lime slurry added based on the current pH monitoring results, and obtains neutralized wastewater by neutralizing the mixed wastewater. The module sets up a detection section perpendicular to the water flow direction at the outlet of the conveying pipe from which the neutralized wastewater enters the sedimentation tank. On the detection section, three fixed sampling positions are dynamically set at the center of the pipe, the upper side at a quarter radius from the pipe wall, and the lower side at a quarter radius from the pipe wall. The three key water quality parameters of pH value, calcium ion concentration and fluoride ion concentration are acquired simultaneously at the three sampling positions. The module constructs a virtual spatial configuration based on three key water quality parameters and calculates the real-time characterization parameters of the spatial configuration. Based on the real-time characterization parameters, a comprehensive correction value is obtained. Based on the comprehensive correction value, the three key water quality parameters are jointly corrected to obtain a set of corrected parameters. The judgment module makes a forward-looking judgment on the formation state and settling trend of the sediment in the sedimentation tank based on the corrected parameters; based on the results of the forward-looking judgment, it adjusts the influent rate of the sedimentation tank in advance or adds flocculant to form sedimentation influent with optimized properties. The processing module introduces the optimized precipitated influent into a sedimentation tank, where it undergoes natural sedimentation to obtain a clear liquid that meets the standards. The clear liquid that meets the standards is then collected for direct discharge or reuse in the production process.

[0071] The above description represents the preferred embodiments of the present invention. It should be noted that those skilled in the art can make various improvements and modifications without departing from the principles of the present invention, and these improvements and modifications should also be considered within the scope of protection of the present invention.

Claims

1. A method for wastewater treatment and control in the clean production of gypsum-based acid manufacturing, characterized in that, The method includes: The wastewater from flue gas scrubbing, equipment cooling, and floor washing is mixed in an equalization tank to form a mixed wastewater. The pH value of the mixed wastewater is monitored in real time to obtain the current pH monitoring results; Based on the current pH monitoring results, the amount of lime slurry added is dynamically adjusted, and the mixed wastewater is neutralized to obtain neutralized wastewater. At the outlet of the conveying pipe from the neutralized wastewater into the sedimentation tank, a detection section is set perpendicular to the water flow direction. On the detection section, three fixed sampling positions are dynamically set at the center of the pipe, the upper side at a quarter radius from the pipe wall, and the lower side at a quarter radius from the pipe wall. The three key water quality parameters of pH value, calcium ion concentration and fluoride ion concentration are acquired simultaneously at the three sampling positions. Based on three key water quality parameters, a virtual spatial configuration is constructed, and the real-time characterization parameters of the spatial configuration are calculated. Based on the real-time characterization parameters, a comprehensive correction value is obtained. Based on the comprehensive correction value, the three key water quality parameters are jointly corrected to obtain a set of corrected parameters. Based on the corrected parameters, a forward-looking judgment is made on the formation state and settling trend of the sediment in the sedimentation tank; based on the results of the forward-looking judgment, the influent rate of the sedimentation tank is adjusted in advance or flocculants are added to form sedimentation influent with optimized properties. The optimized influent is placed in a sedimentation tank and treated by natural sedimentation to obtain a clear liquid that meets the standards. The clear liquid that meets the standards is collected and either discharged directly or reused in the production process.

2. The wastewater treatment and control method in the clean production of gypsum-based acid manufacturing according to claim 1, characterized in that, Wastewater from flue gas scrubbing, equipment cooling, and floor washing is introduced into a regulating tank for mixing to form a mixed wastewater, including: The wastewater from flue gas scrubbing, equipment cooling, and floor washing is introduced into the designated containment area of ​​the equalization tank through independent conveying pipelines. Real-time monitoring of the instantaneous flow rate and pH value of various types of wastewater in the designated containment area; Based on the monitoring results of instantaneous flow rate and pH value, the delivery rate of various types of wastewater flowing into the main mixing zone of the equalization tank is dynamically adjusted; In the main mixing zone of the equalization tank, various types of wastewater that are fed in according to the conveying rate are forcibly mixed and agitated. Forced mixing and agitation promotes the full interaction and diffusion of wastewater with different properties, ultimately forming a mixed wastewater with a relatively uniform water quality distribution.

3. The wastewater treatment and control method in the clean production of gypsum-based acid manufacturing according to claim 2, characterized in that, The pH value of the mixed wastewater is monitored in real time to obtain the current pH monitoring results, including: Inside the main mixing zone of the equalization tank, a spatial array of monitoring points consisting of multiple pH sensors is arranged; By using a spatial array of monitoring points, multiple real-time pH readings of the mixed wastewater at different spatial locations are collected simultaneously. Based on the values ​​of multiple real-time pH readings and their corresponding spatial relationships, a dispersion index is calculated to characterize the pH distribution equilibrium within the entire main mixing zone. Based on the dispersion index, the weighting of the pH readings involved in the final calculation is dynamically adjusted. By weighted fusion of multiple real-time pH readings, a current pH monitoring result that can represent the overall acid-base state of the mixed wastewater is obtained.

4. The wastewater treatment and control method in the clean production of gypsum-based acid manufacturing according to claim 3, characterized in that, Based on the current pH monitoring results, the dosage of lime slurry is dynamically adjusted, and the mixed wastewater is neutralized to obtain neutralized wastewater, including: Based on the current pH monitoring results, the required theoretical amount of lime slurry is calculated by combining the preset target pH range. Based on the theoretical dosage of lime slurry, the lime slurry is injected into the neutralization reaction zone by adjusting the instantaneous flow rate of lime slurry addition; Within the neutralization reaction zone, stirring ensures that the lime slurry and the mixed wastewater come into full contact and undergo a neutralization reaction. During the neutralization reaction, the instantaneous pH value of the effluent from the neutralization reaction zone is monitored in real time and compared with the target pH range; Based on the comparison results, the amount of lime slurry added was finely adjusted in a closed loop to ensure that the pH value of the effluent remained stable within the target pH range; the effluent with a stable pH value within the target pH range was identified as qualified neutralized wastewater.

5. The wastewater treatment and control method in the clean production of gypsum-based acid manufacturing according to claim 4, characterized in that, At the outlet of the conveying pipe from the neutralized wastewater into the sedimentation tank, a detection section is set perpendicular to the water flow direction. On this detection section, three fixed sampling points are dynamically set at the center of the pipe, the upper side at a quarter-radius distance from the pipe wall, and the lower side at a quarter-radius distance from the pipe wall. Simultaneously, three key water quality parameters—pH value, calcium ion concentration, and fluoride ion concentration—are acquired at these three sampling points. The qualified neutralized wastewater flows through the pre-designed conveying pipeline; At the outlet of the conveying pipeline, a detection section is established perpendicular to the direction of wastewater flow; On the inspection section, the center position of the pipe, the upper position at a quarter radius from the pipe wall, and the lower position at a quarter radius from the pipe wall are precisely marked as three specific spatial points; The three specific spatial locations are set as fixed sampling locations; the pH value, calcium ion concentration and fluoride ion concentration at the three sampling locations are collected synchronously within the set time window using a multi-parameter water quality sensor. The pH value, calcium ion concentration, and fluoride ion concentration collected simultaneously were summarized into three key water quality parameters.

6. The wastewater treatment and control method in the clean production of gypsum-based acid manufacturing according to claim 5, characterized in that, Based on three key water quality parameters, a virtual spatial configuration is constructed, and the real-time characterization parameters of the spatial configuration are calculated. A comprehensive correction value is derived based on the real-time characterization parameters; Based on the comprehensive correction values, the three key water quality parameters were jointly corrected to obtain a set of corrected parameters, including: Acquire spatial location information of three sampling sites and the corresponding three key water quality parameters; Based on the spatial location information of the three sampling points, a virtual reference plane is constructed; the key water quality parameters corresponding to the sampling point located at the center of the pipeline are mapped to a theoretical projection point on the virtual reference plane. Calculate the overall deviation between the actual key water quality parameters at the sampling point at the center location and the theoretical projection point; based on the overall deviation, generate an overall correction value; Based on the comprehensive correction value, the original key water quality parameters obtained synchronously from the three sampling locations are jointly corrected. Through joint correction processing, a set of corrected parameters that can more accurately reflect the overall properties of the water body are obtained.

7. The wastewater treatment and control method in the clean production of gypsum-based acid manufacturing according to claim 6, characterized in that, Based on the corrected parameters, a forward-looking judgment is made on the formation state and sedimentation trend of sediments in the sedimentation tank. Based on the results of forward-looking assessments, the influent rate to the sedimentation tank is adjusted in advance or additional flocculants are added to create optimized sedimentation influent, including: The corrected parameters were compared and analyzed with the preset empirical thresholds for precipitate formation and sedimentation. Based on the comparative analysis results, the formation rate and settling velocity of sediment in the sedimentation tank under the current water quality conditions are predicted. Based on the predicted generation rate and settling velocity, determine whether the operating conditions of the sedimentation tank need to be adjusted; When the predicted settling velocity is lower than the formation rate, reduce the influent rate of the sedimentation tank or start the flocculant addition process. By adjusting the influent rate or adding flocculants, the properties of the wastewater to be treated are optimized, resulting in optimized precipitated influent.

8. The wastewater treatment and control method in the clean production of gypsum-based acid manufacturing according to claim 7, characterized in that, The optimized influent is placed in a sedimentation tank and treated by natural sedimentation to obtain a clear liquid that meets the standards. Clear liquids that meet the standards are collected for direct discharge or reuse in the production process, including: The optimized influent is introduced into the uniform water distribution zone of the sedimentation tank; within the sedimentation tank, suspended solids and the generated CaF2 and Ca3(PO4)2 precipitates are naturally separated by gravity. After the set set settling time is reached, water samples are collected from the clear water area at the top of the sedimentation tank, and the turbidity and key ion concentration of the water samples are monitored. The monitoring results are compared and verified with the preset emission or reuse standards; When the verified monitoring results meet the standards, the qualified clear liquid is collected for direct discharge or reuse in the production process. When the verified monitoring results do not meet the standards, a portion of the clarified liquid is returned to the equalization tank for further treatment.

9. A wastewater treatment and control system for clean production of gypsum-based acid, the system implementing the method as described in any one of claims 1 to 8, characterized in that, include: The monitoring module is used to mix the flue gas scrubbing wastewater, equipment cooling wastewater and ground flushing wastewater in the equalization tank to form mixed wastewater; The pH value of the mixed wastewater is monitored in real time to obtain the current pH monitoring results; The adjustment module dynamically adjusts the amount of lime slurry added based on the current pH monitoring results, and obtains neutralized wastewater by neutralizing the mixed wastewater. The module sets up a detection section perpendicular to the water flow direction at the outlet of the conveying pipe from which the neutralized wastewater enters the sedimentation tank. On the detection section, three fixed sampling positions are dynamically set at the center of the pipe, the upper side at a quarter radius from the pipe wall, and the lower side at a quarter radius from the pipe wall. The three key water quality parameters of pH value, calcium ion concentration and fluoride ion concentration are acquired simultaneously at the three sampling positions. The module constructs a virtual spatial configuration based on three key water quality parameters and calculates the real-time characterization parameters of the spatial configuration. A comprehensive correction value is derived based on the real-time characterization parameters; Based on the comprehensive correction value, the three key water quality parameters are jointly corrected to obtain a set of corrected parameters; The judgment module makes a forward-looking judgment on the formation state and settling trend of the sediment in the sedimentation tank based on the corrected parameters; based on the results of the forward-looking judgment, it adjusts the influent rate of the sedimentation tank in advance or adds flocculant to form sedimentation influent with optimized properties. The processing module introduces the optimized precipitated influent into a sedimentation tank, where it undergoes natural sedimentation to obtain a clear liquid that meets the standards. The clear liquid that meets the standards is then collected for direct discharge or reuse in the production process.

10. A computing device, characterized in that, include: One or more processors; A storage device for storing one or more programs that, when executed by one or more processors, cause the one or more processors to implement the method as described in any one of claims 1 to 9.

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