Method for monitoring concentration of water body disinfection by-products based on electron donating capability

Abstract

The invention discloses a method for monitoring the concentration of a water body disinfection by-product DBPs based on electron donating ability, and belongs to the technical field of environmental engineering.The method comprises the steps that S1, a water body sample is collected, first pretreatment is conducted, and the EDC value is measured through an ABTS + free radical reduction decolorization method; s2, carrying out second pretreatment on the water body sample subjected to the first pretreatment, and measuring the concentrations of trihalomethane and haloacetic acid in the water body sample by utilizing a gas chromatographic method; s3, by taking the EDC value as an independent variable and the trihalomethane concentration and the haloacetic acid concentration as dependent variables, establishing a first prediction model for predicting the trihalomethane concentration based on the EDC value and a second prediction model for predicting the haloacetic acid concentration based on the EDC value; and S4, predicting the concentration of trihalomethane and the concentration of haloacetic acid by using the first prediction model and the second prediction model based on the EDC value of the target to-be-detected water body sample. The method solves the problems that a traditional DBPs detection method is long in time consumption and complex in operation.

Description

TECHNICAL FIELD

[0001] The application belongs to the technical field of environmental engineering, and particularly relates to a method for monitoring the concentration of disinfection by-products in water based on electron donation capacity. BACKGROUND

[0002] Drinking water disinfection process can generate a variety of disinfection by-products (DBPs) with low concentration of ng~μg L -1 level in water while killing pathogens. These DBPs have potential harm to human health and are important water quality monitoring indicators. Traditional DBP monitoring methods mainly rely on instrument analysis methods such as gas chromatography (GC), gas chromatography-mass spectrometry (GC-MS), and liquid chromatography-mass spectrometry (LC-MS). For example, the Chinese patent document with publication number CN111351890A discloses a method for detecting halogenated pyridine alcohol disinfection by-products in water. The method first pretreats the water sample to obtain a test solution, uses liquid chromatography-mass spectrometry to detect halogenated pyridine alcohol disinfection by-products in the test solution, establishes a working curve of halogenated pyridine alcohol disinfection by-products, and obtains a spectrum of the test substance. The concentration of halogenated pyridine alcohol disinfection by-products is calculated by using the external standard method. For example, the Chinese patent document with publication number CN111307989A discloses a method for simultaneously determining trihalomethane and halogen acetonitrile in water. The method combines liquid-liquid extraction and gas chromatography to simultaneously determine a variety of common carbon-containing and nitrogen-containing disinfection by-products in water.

[0003] Although the above methods have high detection accuracy, they have problems such as expensive equipment, complex operation, and long detection period, which are difficult to meet the needs of real-time monitoring and rapid response of water quality. In addition, the generation of DBPs is affected by many factors such as the content of organic matter in water, pH, temperature, residual chlorine concentration, and hydraulic retention time. A single parameter cannot accurately reflect the generation potential.

[0004] Electron donation capacity (EDC) is widely used in antioxidant capacity evaluation and water organic load analysis as an index of the comprehensive activity of reducing substances in water. This index deeply reveals the redox characteristics of dissolved organic matter (DOM) and is crucial for understanding the migration, transformation, and degradation process of pollutants in water and ecological risk. In addition, EDC reflects the total amount of oxidizable organic and inorganic substances in water. Through EDC value, the electron donation capacity of various reducing substances such as humic acid, fulvic acid, amino acid, and reducing sugar can be comprehensively characterized, which can reflect the potential of precursors to generate DBPs by reacting with chlorine.

[0005] EDC as an important comprehensive index in the cross field of environmental chemistry, hydrology and ecology, if a method for determining water EDC and combining data modeling to realize the rapid evaluation of water DBP concentration can be developed, it will help to improve the water quality monitoring efficiency and risk warning ability. SUMMARY

[0006] The application provides a method for monitoring water disinfection by-product concentration based on electron donating capacity, which utilizes ABTS + EDC value of water sample is determined by ABTS free radical cation reduction decolorization method, and a prediction model is established by combining historical DBP concentration data, so that rapid monitoring and pollution risk warning of typical disinfection by-products such as trihalomethane THM and haloacetic acid HAA can be realized.

[0007] The specific technical solutions are as follows: A method for monitoring water disinfection by-product concentration based on electron donating capacity, the disinfection by-products include trihalomethane and haloacetic acid, and the method comprises the following steps: S1: collecting different water samples, performing first pretreatment, and determining EDC value of the pretreated water sample by ABTS + free radical reduction decolorization method; S2: performing second pretreatment on the water sample pretreated in step S1, and determining the concentration of trihalomethane and haloacetic acid in the water sample by gas chromatography; S3: taking the EDC value measured in step S1 as the independent variable, and taking the concentration of trihalomethane and the concentration of haloacetic acid measured in step S2 as the dependent variables, to establish a first prediction model for predicting the concentration of trihalomethane based on EDC value and a second prediction model for predicting the concentration of haloacetic acid based on EDC value; S4: determining the EDC value of the target water sample to be measured according to the method in step S1, and substituting the EDC value into the first prediction model and the second prediction model to calculate the concentration of trihalomethane and the concentration of haloacetic acid in the target water sample to be measured; In step S1, in the phosphate buffer system, the experimental group water sample or the blank control sample and ABTS + working solution react for 10-30 min, and the absorbance of the experimental group water sample and the absorbance of the blank control sample are determined A 水样 A 空白 EDC value is calculated by the following formula;

[0008] Among them, A 水样 ​is the absorbance of the water sample in the experimental group; A 空白 is the absorbance of the blank control sample; ε ABTS· + is the molar absorption coefficient of ABTS· + , unit: L mol -1 cm -1 ; is the optical path, unit: cm; C DOC is the dissolved organic carbon DOC concentration in the reaction system, unit: mg L -1 .

[0009] Studies have shown that there is a significant positive correlation between the EDC value and the concentration of trihalomethane THMs and haloacetic acid HAAs, which has the potential to be a fast prediction index of DBPs, the present application determines the EDC value of natural organic matter and inorganic reducing substances in the water sample by ABTS· + radical reduction decolorization method, establishes the quantitative relationship between the EDC value and the concentration of main disinfection by-products DBPs such as trihalomethane THMs and haloacetic acid HAAs, and realizes the rapid evaluation of DBP generation potential and pollution risk warning by analyzing the dynamic correlation between the EDC value and the concentration of DBPs.

[0010] Further, the trihalomethane includes chloroform, monobromodichloromethane or tribromomethane; and the haloacetic acid includes chloroacetic acid, bromoacetic acid or dichloroacetic acid.

[0011] Preferably, the first pretreatment step is: adding sodium thiosulfate to quench the oxidizing agent in the water sample, and then removing the suspended particles in it by using a microporous filter membrane.

[0012] Further, in step S1, ultrapure water is used as a blank control sample, and the absorbance of the water sample in the experimental group is measured at 728nm A 水样 and the absorbance of the blank control sample A 空白 .

[0013] Preferably, in step S2, when the concentration of trihalomethane is determined by gas chromatography, the second pretreatment step is: adding anhydrous sodium sulfate to the first pretreated water sample, dissolving, then adding an internal standard and an extractant methyl tert-butyl ether, extracting, and then taking the upper organic phase for gas chromatography analysis; the parameter conditions for gas chromatography analysis are: a chromatographic column HP-5MS UI capillary column; a sample injection volume of 0.5 μL; a sample injection port temperature of 220°C; a carrier gas flow rate of 30 mL / min; a temperature rising program of: 33°C for 10 min, rising to 75°C at a rate of 18°C / min, maintaining for 1.5 min, then rising to 170°C at a rate of 45°C / min, maintaining for 2 min; and an ECD detector temperature of 250°C.

[0014] Preferably, in step S2, when the concentration of haloacetic acid is determined by gas chromatography, the second pretreatment step is: adding sulfuric acid and anhydrous sodium sulfate to the first pretreated water sample, dissolving, then adding an internal standard and an extractant methyl tert-butyl ether, extracting, and then taking the upper organic phase to add acidified methanol for derivation and esterification reaction, then adding a sodium sulfate solution, taking the upper organic phase after the solution is left to stand and stratify, adding a saturated sodium bicarbonate solution, mixing thoroughly, and then taking the upper organic phase for gas chromatography analysis; the parameter conditions for gas chromatography analysis are: a chromatographic column HP-5MS UI capillary column; a sample injection volume of 0.5 μL; a sample injection port temperature of 230°C; a carrier gas flow rate of 30 mL / min; a temperature rising program of: 35°C for 13 min, rising to 200°C at a rate of 30°C / min, maintaining for 4 min; and an ECD detector temperature of 300°C.

[0015] Preferably, the water sample data used to establish the first prediction model or the second prediction model is ≥ 40 groups.

[0016] Specifically, the first prediction model and the second prediction model are both linear regression models.

[0017] Further, in step S4, the first prediction model is expressed as C THMs= k 1 × EDC + b1, wherein C THMs is the concentration of trihalomethane, EDC represents the EDC value, k 1 and b1 is a first prediction model parameter; and the second prediction model is expressed as C HAAs= k 2 × EDC + b2, wherein C HAAs is the concentration of haloacetic acid, EDC represents the EDC value, k 2 and b2 is a second prediction model parameter.

[0018] The prediction effect of the method is good, and experiments prove that the error between the concentration of trihalomethane predicted by the first prediction model and the concentration of haloacetic acid predicted by the second prediction model and the actual detection data of the gas chromatography method is less than 10%.

[0019] Compared with the prior art, the method has the beneficial effects that: (1) In actual application, based on the established first prediction model and second prediction model, ABTS· + After the EDC value of the water sample is determined by the free radical reduction decolorization method, the concentration of the disinfection by-product can be predicted, and the single detection time is less than 15 minutes, which is much lower than the several hours required by the traditional GC-MS method. (2) The method can complete the determination of the EDC value on the sampling site or in an online monitoring system, without complex pretreatment steps such as extraction or derivatization, so that the time from sampling to result output is greatly shortened. (3) The method requires simple equipment, and after the first prediction model and the second prediction model are established, only an ultraviolet-visible spectrophotometer or a microplate reader is required to realize detection, thereby reducing the detection cost. (4) After the first prediction model and the second prediction model are established, the method is easy to operate, has low requirements for the professionalism of the operator, and can realize large-scale engineering popularization and application. BRIEF DESCRIPTION OF DRAWINGS

[0020] Figure 1 (a) is the linear correlation analysis result of the EDC value and the concentration of trihalomethane in the first prediction model of Example 1, and (b) is the linear correlation analysis result of the EDC value and the concentration of haloacetic acid in the second prediction model of Example 1.

[0021] Figure 2 The results of the comparison between the predicted values of the concentration of trihalomethane and haloacetic acid by the EDC method and the measured values by the GC method in Example 2, wherein (a) is the concentration of trihalomethane, and (b) is the concentration of haloacetic acid.

[0022] Figure 3 The results of the comparison between the predicted values of the concentration of trihalomethane and haloacetic acid by the EDC method and the measured values by the GC method in Example 3, wherein (a) is the concentration of trihalomethane, and (b) is the concentration of haloacetic acid. DETAILED DESCRIPTION

[0023] For the purposes of making the objects, features, and advantages of the present application clearer, more apparent and easier to understand, specific embodiments will be described in detail below. Numerous specific details are set forth in the following description in order to provide a thorough understanding of the present application. However, the present application can be practiced according to many different embodiments other than those described herein without departing from the scope of the present application, and it can be understood that similar changes in form and function are intended to be within the scope of the present application. Therefore, the present application is not limited to the specific embodiments disclosed below, but rather, covers all modifications and changes falling within the scope of the present application.

[0024] The operation methods not specified in the following examples are generally performed according to the conventional conditions, or according to the conditions suggested by the manufacturers. The contents not described in detail in the specification belong to the prior art known to those skilled in the art. The experimental materials used in the following examples can be purchased from the conventional biochemical reagent companies, unless otherwise specified.

[0025] Example 1 (1) A total of 41 groups of water samples were collected from different locations of a water plant or a water supply network, and 2 g / L sodium thiosulfate was immediately added to quench the oxidizing agent in the water samples after the water samples were collected, and 0.45 μm microporous filter membranes were used to filter and remove suspended particles (first pretreatment), and the water samples were stored at 4°C in the dark; then ABTS· + radical reduction decolorization method was used to determine the EDC values of the water samples pretreated in the above steps; the ABTS· + radical reduction decolorization method specifically includes the following steps: ABTS was dissolved in 7.5 mmol / L H2SO4 (pH = 2.0) to prepare a 1 mmol / L ABTS solution. Then 1 mL of the ABTS solution was mixed with 0.35 mL of a 10 mmol / L NaClO solution and 4 μL of a 3 mol / L H2SO4 solution to prepare an ABTS· -1 solution. -1 -1 +

[0026] In a 10 mL centrifuge tube, 3 mL of the experimental water sample or the blank sample (ultra-pure water) and 1.5 mL of a 100 mmol / L phosphate buffer were sequentially added; then 0.5 mL of the ABTS· -1 solution was added to start the reaction, and after 15 min of reaction, the absorbance was determined at 728 nm using a cuvette with an optical path of 10 mm; + The EDC values of different water samples were calculated using the measured absorbance:

[0027] wherein, A ​​​​水样 Absorbance of water sample for experimental group A 空白 Absorbance of control sample for blank group ε ABTS· + Molar absorption coefficient of ABTS· + (728 nm, 14 000 L mol -1 cm -1 -1 cm Optical path length, unit: cm C DOC Dissolved organic carbon (DOC) concentration in reaction system, unit: mg L -1

[0028] (2) The second pretreatment was performed on the water sample pretreated in step (1), and the concentrations of trihalomethane and haloacetic acid were determined by gas chromatography.

[0029] When determining the concentration of trihalomethane by gas chromatography, liquid-liquid extraction method was adopted: 4 g of anhydrous sodium sulfate was weighed and added to 25 mL of the water sample pretreated in the first step, and then dissolved by shaking rapidly; subsequently, 2 mL of methyl tert-butyl ether extractant containing 150 μg / L of internal standard 1,2-dibromopropane was added, and shaken for 5 minutes to ensure complete extraction; after 5 minutes of standing to form a clear interface, the upper organic phase was transferred to a 2 mL sample bottle for gas chromatography analysis.

[0030] When determining the concentration of haloacetic acid by gas chromatography, liquid-liquid microextraction combined with acidified methanol esterification method was adopted: 30 mL of the water sample pretreated in the first step was taken, and 2 mL of sulfuric acid was added. After adding 4 g of anhydrous sodium sulfate, it was shaken vigorously to ensure complete dissolution. Then, 3 mL of methyl tert-butyl ether solution containing 300 μg / L of internal standard 1,2-dibromopropane was added as an extractant. After mixing thoroughly, it was allowed to stand for 5 minutes to ensure complete extraction. Subsequently, the upper organic phase was collected and transferred to a 10 mL capacity derivative bottle. 2 mL of acidified methanol (concentrated sulfuric acid and methanol were mixed at a volume ratio of 1:10) was added to the derivative bottle, the bottle cap was tightly closed, and it was shaken thoroughly to complete the derivation process. The derivative bottle was placed in a 50°C water bath for 2 hours for esterification reaction. After the esterification reaction, the container was cooled to room temperature, 7 mL of 150 g / L sodium sulfate solution was added, and it was allowed to stand to separate the layers. The upper organic layer was transferred to a 2 mL capacity bottle, followed by the addition of 1 mL of saturated sodium bicarbonate solution, and it was shaken to ensure thorough mixing and release any gas, and then it was allowed to stand for 3 minutes. Finally, the upper organic phase after the above treatment was transferred to the sample bottle for gas chromatography analysis.

[0031] Further gas chromatography determination parameters are shown in Table 1: ​Table 1 Gas chromatography method of trihalomethane and haloacetic acid

[0032] A standard curve was made, and the concentration of trihalomethane and haloacetic acid in the water body was calculated by using the standard curve; series standard solutions with trihalomethane concentrations of 5, 10, 15, 20, 50 μg / L and haloacetic acid concentrations of 1, 5, 10, 15, 20 μg / L were removed and pretreated. After determination by gas chromatography, the standard curve R 2 of trihalomethane was 0.999, the standard curve R 2 of monobromodichloromethane was 0.998, the standard curve R 2 of tribromomethane was 0.999; the standard curve R THMs of haloacetic acid was 0.998, the standard curve R 1 of chloroacetic acid was 0.999, and the standard curve R THMs of dichloroacetic acid was 0.997, wherein R 1 is a dimensionless index for measuring the goodness of fit of the regression straight line to the data points.

[0033] (3) The EDC values measured by the above steps were taken as independent variables, and the trihalomethane concentration and the haloacetic acid concentration were taken as dependent variables, to establish a first prediction model for predicting the trihalomethane concentration based on the EDC value and a second prediction model for predicting the haloacetic acid concentration based on the EDC value; both the first prediction model and the second prediction model were linear regression models. The first prediction model was represented as C HAAs = k 2 ×EDC+b1, wherein C HAAs THMs represents the trihalomethane concentration, EDC represents the EDC value, k 2 and b1 are the parameters of the first prediction model; the second prediction model was represented as C HAAs = k 2 ×EDC+b2, wherein C HAAs HAAs represents the haloacetic acid concentration, EDC represents the EDC value, k 2 and b2 are the parameters of the second prediction model.

[0034] Analysis showed that the correlation coefficients between the EDC and THMs and HAAs of 41 water samples were R1 2 0.89 and R1 2 0.82, respectively, and the correlation was good. Figure 1 .

[0035] Example 2 Six sets of water samples were collected from different locations in the water plant or pipeline network compared to Example 1. Immediately after collection, 2 g / L sodium thiosulfate was added to quench the oxidant. Suspended particles were removed by filtration through a 0.45 μm microporous membrane and the samples were stored at 4°C in the dark. The EDC values ​​of the six sets of water samples were then measured using the same method as in Example 1. The concentrations of trihalomethanes (THMs) and haloacetic acids (HAAs) were predicted using the first and second prediction models established in Example 1. Simultaneously, the actual values ​​of the trihalomethane (THMs) and haloacetic acid (HAAs) concentrations of the six sets of water samples were determined using the same gas chromatography method as in Example 1, and compared with the values ​​calculated using the EDC method. The results are as follows: Figure 2 As shown.

[0036] Depend on Figure 2 It can be seen that the error ranges of THMs concentration and HAAs concentration calculated using EDC values ​​are 2.6%-8.1% and 1.5%-9.7%, respectively. Therefore, it can be concluded that EDC can accurately reflect the concentration of disinfection byproducts in water samples.

[0037] Example 3 Sampling was conducted on a specific node of the water supply network for 15 consecutive days. Immediately after sampling, 2 g / L sodium thiosulfate was added to quench the oxidant. The samples were then filtered through a 0.45 μm microporous membrane to remove suspended particles and stored at 4°C in the dark. Subsequently, the EDC values ​​of the 15 water samples were determined using the same method as in Example 1. The concentrations of trihalomethanes (THMs) and haloacetic acids (HAAs) were predicted using the first and second prediction models established in Example 1. Simultaneously, the actual values ​​of the trihalomethane (THMs) and haloacetic acid (HAAs) concentrations of the 15 water samples were determined using the same gas chromatography method as in Example 1, and compared with the values ​​calculated using the EDC method. The results are as follows: Figure 3 As shown.

[0038] Depend on Figure 3 It can be seen that the error range between the THMs concentration calculated by EDC and the measured THMs concentration is 0.9%-8.3%, and the error range between the HAAs concentration calculated by EDC and the measured HAAs concentration is 0.07%-9.2%, indicating that the method of calculating the concentration of disinfection byproducts in water samples by EDC has good stability.

[0039] The embodiments described above provide a detailed explanation of the technical solutions of the present invention. It should be understood that the above descriptions are merely specific embodiments of the present invention and are not intended to limit the present invention. Any modifications, additions, or similar substitutions made within the scope of the principles of the present invention should be included within the protection scope of the present invention.

Claims

1. A method for monitoring disinfection by-product concentration in a body of water based on electronic capacity, characterized by, The disinfection by-products include trihalomethane and haloacetic acid, and the method comprises the following steps: S1: Collect different water samples, perform the first pretreatment, and use ABTS• + EDC value of the pretreated water sample is determined by free radical reduction decolorization method; S2: the second pretreatment is performed on the water sample after the first pretreatment in step S1, and the concentrations of trihalomethane and haloacetic acid in the water sample are determined by using gas chromatography; S3: the EDC value measured in step S1 is taken as an independent variable, and the concentrations of trihalomethane and haloacetic acid measured in step S2 are taken as dependent variables, so as to establish a first prediction model for predicting the concentration of trihalomethane based on the EDC value and a second prediction model for predicting the concentration of haloacetic acid based on the EDC value; S4: the EDC value of the target water sample to be measured is determined by using the method in step S1, and the EDC value is substituted into the first prediction model and the second prediction model, so as to calculate the concentrations of trihalomethane and haloacetic acid in the target water sample to be measured. In step S1, the experimental group water sample or the blank group control sample and ABTS• + The working solution was reacted for 10-30 min, and the absorbance of the experimental group water sample was determined A 水样 and the absorbance of the blank group control sample A 空白 The EDC value was calculated by the following formula; wherein, A 水样 is the absorbance of the water sample of the experimental group; A 空白 is the absorbance of the control sample of the blank group; ε ABTS· + is the ABTS· + is the molar absorption coefficient of ABTS· -1 cm -1 ; is the optical path length, in cm; C DOC is the dissolved organic carbon (DOC) concentration in the reaction system, in mg L -1 .

2. The method for monitoring disinfection byproduct concentrations in a body of water based on supplied electrical capacity of claim 1, wherein, The trihalomethane includes chloroform, monobromodichloromethane or tribromomethane; and the haloacetic acid includes chloroacetic acid, bromoacetic acid or dichloroacetic acid.

3. The method for monitoring disinfection byproduct concentrations in a body of water based on supplied electrical capacity of claim 1, wherein, The first pretreatment step is that sodium thiosulfate is added to the water sample to quench the oxidant, and then a microporous filter membrane is used to filter and remove suspended particles in the water sample.

4. The method for monitoring disinfection byproduct concentrations in a body of water based on supplied electrical capacity of claim 1, wherein, In step S1, using ultrapure water as a blank control sample, the absorbance of the experimental group water sample is determined at 728 nm A 水样 and the absorbance of the blank control sample A 空白 .

5. The method for monitoring the concentrations of disinfection by-products in water bodies based on electron donating capacity according to claim 1, wherein, In step S2, when the concentration of trihalomethane is determined by using gas chromatography, the second pretreatment step is that anhydrous sodium sulfate is added to the water sample after the first pretreatment, and then an internal standard and an extractant methyl tert-butyl ether are added after dissolution, and the upper organic phase is taken after extraction for gas chromatography analysis; the parameter conditions for gas chromatography analysis are as follows: a chromatographic column HP-5MS UI capillary column; a sample injection volume of 0.5 μL; a sample injection port temperature of 220℃; a carrier gas flow of 30 mL / min; and a temperature rising program of 33℃ for 10 min, rising to 75℃ at a rate of 18℃ / min and maintaining for 1.5 min, then rising to 170℃ at a rate of 45℃ / min and maintaining for 2 min; and an ECD detector temperature of 250℃.

6. The method for monitoring disinfection byproduct concentrations in a body of water based on supplied electrical capacity of claim 1, wherein, In step S2, when the concentration of haloacetic acid is determined by using gas chromatography, the second pretreatment step is that sulfuric acid and anhydrous sodium sulfate are added to the water sample after the first pretreatment, and then an internal standard and an extractant methyl tert-butyl ether are added after dissolution, and the upper organic phase is taken after extraction for gas chromatography analysis; the parameter conditions for gas chromatography analysis are as follows: a chromatographic column HP-5MS UI capillary column; a sample injection volume of 0.5 μL; a sample injection port temperature of 230℃; a carrier gas flow of 30 mL / min; and a temperature rising program of 35℃ for 13 min, rising to 200℃ at a rate of 30℃ / min and maintaining for 4 min; and an ECD detector temperature of 300℃.

7. The method for monitoring disinfection byproduct concentrations in a body of water based on supplied power capacity of claim 1, wherein, The water sample data for establishing the first prediction model or the second prediction model is ≥40 groups.

8. The method for monitoring disinfection byproduct concentrations in a body of water based on supplied electrical capacity of claim 1, wherein, The first prediction model and the second prediction model are both linear regression models.

9. The method for monitoring disinfection byproduct concentrations in a body of water based on supplied power capacity according to claim 8, wherein, the first prediction model is represented as C THMs = a0 + a1 x EDC + b1 k 1 where THMs is the trihalomethane concentration, EDC represents the EDC value, C THMs = a0 + a1 x EDC + b1 k 1 and b1 are the first prediction model parameters; the second prediction model is represented as C HAAs = a0 + a1 x EDC + b2 k 2 where HAAs is the haloacetic acid concentration, EDC represents the EDC value, C HAAs = a0 + a1 x EDC + b2 k 2 and b2 are the second prediction model parameters.

10. The method for monitoring disinfection byproduct concentrations in a body of water based on supplied power capacity of claim 1, wherein, The error of the concentration of the trihalomethane predicted by the first prediction model and the concentration of the haloacetic acid predicted by the second prediction model is less than 10% compared with the actual detection data of the gas chromatography method.

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