A permeable reaction wall device and filler for acidic mine water treatment

Abstract

The present invention belongs to the technical field of permeable reaction devices, and specifically relates to a novel multi-segment spliced ​​structure permeable reaction wall device and filler for treating acidic mineral water. The device is composed of multiple connected wall sections, with an inverted trapezoidal water channel provided in the middle of the wall. Several slots are evenly arranged on the wall within the water channel, and filter plates are movably provided in the slots. The device comprises a novel composite filler composed of fly ash, nano-ferroferric oxide, and quartz sand. The novel permeable reaction wall filler of the present invention is used to treat acidic mineral water, and the novel multi-segment spliced ​​structure permeable reaction wall device can be used to treat various water pollution.

Description

Technical Field

[0001] The invention belongs to the technical field of permeable reaction devices, and in particular relates to a permeable reaction wall device and filler for acidic mineral water treatment. Background Art

[0002] With the rapid development of industry, the demand for mineral resources in countries around the world has gradually increased. The large-scale mining and utilization of coal has led to increasingly serious problems of mine environmental pollution, especially the pollution of mine wastewater. It has become a global problem, among which acidic mine wastewater is the most serious.

[0003] Permeable Reactive Wall Technology: Permeable Reactive Wall (PRB) is a passive remediation technology for in-situ water pollution control. It targets the specific components of polluted water (such as acid mine drainage) by placing a reactive material treatment zone downstream. Physical, chemical, or biological treatment techniques are used to treat the pollutants flowing through the wall, achieving a treatment effect tailored to local conditions. Features include: no external power required, the reactive wall is constructed within the mine entrance, taking up no floor space, economical and convenient treatment, and the wall filling material is replaceable.

[0004] Existing permeable reaction wall devices include funnel-gate and continuous reaction wall types. The funnel-gate reaction wall uses gates to divert water, ensuring full contact between the water and the filler. The continuous reaction wall utilizes multiple connected reaction wall systems to increase the contact area between the filler and the water. The reactive medium installed in traditional reaction wall structures is a fixed installation, typically cast integrally with the wall and installed in the water, making it difficult to clean and replace the reactive medium. Summary of the Invention

[0005] In view of the above problems, the present invention provides a permeable reaction wall device and filler for acidic mine water treatment.

[0006] In order to achieve the above object, the present invention adopts the following technical solutions:

[0007] A permeable reaction wall device for acidic mineral water treatment is composed of multiple wall sections connected together. An inverted trapezoidal water channel is arranged in the middle of the wall. Several slots are evenly arranged on the wall inside the water channel, and filter plates are movably arranged in the slots.

[0008] Furthermore, the upper end of the slot is tilted backward so that the filter plate can be placed tilted.

[0009] Furthermore, hollow channels are provided in the walls on both sides of the water channel, a concentration detector is provided in the hollow channel, and a diversion hole connected to the water channel is provided at the bottom of the hollow channel for passing through a pipeline to transport the water in the water channel to the concentration detector.

[0010] Furthermore, a water pump is provided in the hollow channel, and a water outlet hole communicating with the water channel is provided at the bottom of the hollow channel for passing a pipe connected to the water outlet end of the water pump.

[0011] Furthermore, the connection between the multiple sections of the wall can be in parallel, in series, stacked up and down, or any combination thereof.

[0012] Furthermore, a filler layer is provided between the connecting gaps of the plurality of wall sections to maintain the continuity between adjacent walls.

[0013] Furthermore, opening and closing doors are provided at the entrance and exit of the hollow passage formed by the multiple sections of the wall connected together to achieve the closure of the hollow passage.

[0014] Furthermore, the filter plate is composed of a middle plate-shaped filler layer and a filter mesh wrapped around the outer side of the plate-shaped filler layer.

[0015] A filler for a permeable reaction wall device used in acidic mineral water treatment, comprising fly ash, nano-ferroferric oxide and quartz sand in a mass ratio of 8:0.5 to 2:4, and applied to a plate-shaped filler layer.

[0016] The invention discloses an application of a permeable reaction wall device for treating acidic mine water, which is used to treat acidic mine water pollution.

[0017] Compared with the prior art, the present invention has the following advantages:

[0018] 1. The permeable reaction wall device of the present invention is composed of multiple wall sections connected in a variety of ways. It can be connected in series, in parallel or stacked up and down according to the specific terrain, which is conducive to space saving and the construction of the permeable reaction wall device.

[0019] 2. The filter plate of the present invention is movable and can be easily cleaned and replaced. When necessary, filter plates with different plate-shaped filler layers can be installed in the same water channel.

[0020] 3. The filter plate of the present invention is arranged at an angle, which is firstly beneficial to increase the filtration area, and secondly, it utilizes the characteristic that the speed of the upper water flow through the filter plate is greater than the speed of the lower water flow through the filter plate, which can realize the position exchange of the upper and lower water flows, that is, the upper water layer first passes through the filter plate and then falls into the lower layer, and the lower water layer passes through the filter plate and is exchanged to the upper layer.

[0021] 4. The present invention sets hollow channels in the walls on both sides of the water channel, and sets concentration detectors in the hollow channels to detect the concentration in the water channel in real time.

[0022] 5. The present invention sets a water pump in the hollow channel, which can realize the placement of the wall outside the polluted water body, and then use the water pump to pump the polluted water into the water channel, avoiding the long-term contact of the wall with acidic water in traditional construction, resulting in wall corrosion.

[0023] 6. The present invention can realize multiple application modes. The first is the immersed tube construction form, in which the manufactured wall structure is placed in the acid mine water body in the form of a immersed tube, allowing the water to flow freely through the water channel and the filter plate, and the height of the water channel must be higher than the horizontal plane height; the second is external construction, in which the wall is placed outside the acid mine water environment, and the contaminated water is pumped into the water channel by pumping. If this form is adopted, an outlet connected to the pump pipe needs to be opened on the inclined surface of the water channel.

[0024] 7. Fly ash and coal-based activated carbon are evenly mixed as a reflective filler, whether it is the removal effect of heavy metals or NH4 + 、SO4 2- The removal effect is better than that of using coal-based activated carbon alone; fly ash and nano-ferroferric oxide mixed as fillers have the effect of removing other heavy metals, heavy metal ions and NH4 + 、SO4 2- The treatment efficiency is higher than that of fly ash as a single filler.

[0025] 8. It not only makes better use of solid waste fly ash as a resource and turns waste into treasure, but also makes it easier to recycle fillers, which is beneficial to the reuse of materials and the centralized treatment of pollutants. BRIEF DESCRIPTION OF THE DRAWINGS

[0026] Figure 1 It is a front view of the wall of the present invention;

[0027] Figure 2 It is a front cross-sectional view of the wall of the present invention;

[0028] Figure 3 is a side view of the present invention;

[0029] Figure 4 is a side sectional view of the wall of the present invention;

[0030] Figure 5 It is a structural schematic diagram of the wall of the present invention;

[0031] Figure 6 is a cross-sectional view of a filter plate of the present invention;

[0032] Figure 7 This is a schematic diagram of the structure of the series connection of walls in Example 1 of the present invention;

[0033] Figure 8 This is a schematic diagram of the structure of parallel connection of walls in Example 2 of the present invention;

[0034] Figure 9 This is the graph showing the change of the removal rate of each element of column 5 over time;

[0035] Figure 10 This is the graph showing the change of the removal rate of each element of column 6 over time;

[0036] Figure 11 This is the graph showing the change of the removal rate of each element of column 7 over time;

[0037] Figure 12 This is the graph showing the change of the removal rate of each element of column 8 over time;

[0038] Figure 13 The removal rate of heavy metals Cu, Zn and Mn by the combined filler changes with time;

[0039] Figure 14 Schematic diagram of the sampling locations at Shandi River;

[0040] Figure 15 Bacterial community distribution map of each sampling point at the genus level;

[0041] Figure 16 Iron-oxidizing bacteria activity assay;

[0042] Figure 17 SEM image of sample 1 (acidic mineral water);

[0043] Figure 18 SEM photo of sample 2 (after treatment);

[0044] Figure 19 X-ray energy spectrum analysis diagram of samples before and after acid mine water treatment;

[0045] In the figure, wall 1, water channel 2, slot 3, filter plate 4, hollow channel 5, concentration detector 6, diversion hole 7, water pump 8, water outlet 9, opening and closing door 10, connection hole 11, metal connecting plate 12, caulking agent layer 13, plate-shaped filler layer 14, and filter screen 15. DETAILED DESCRIPTION

[0046] In order to further illustrate the technical solution of the present invention, the present invention is further described below through examples.

[0047] Example 1

[0048] like Figures 1 to 7As shown, a permeable reaction wall device for acidic mineral water treatment is composed of multiple wall sections 1 connected in series. A caulking layer 13 is provided between the connecting gaps of the multiple wall sections 1 to maintain continuity between adjacent wall sections 1. Connection holes 11 are provided at the edges of the wall sections 1, and bolts are installed in the connection holes 11. Metal connecting plates 12 are installed on the bolts on adjacent wall sections 1 to secure the adjacent wall sections 1. An inverted trapezoidal water channel 2 is provided in the middle of the wall section 1. Several slots 3 are evenly arranged on the wall within the water channel 2. The upper ends of the slots 3 are tilted backward, and filter plates 4 are movably installed in the slots 3. The filter plates 4 are composed of a central plate-shaped filler layer 14 and a filter mesh 15 wrapped around the outer surface of the plate-shaped filler layer 14. Hollow channels 5 are provided in the walls on both sides of the water channel 2. A concentration detector 6 is installed within the hollow channel 5. A diversion hole 7 is provided at the bottom of the hollow channel 5, communicating with the water channel 2. This hole is used to pass a pipe through the water channel 2 and transport the water in the water channel 2 to the concentration detector 6. A water pump 8 is also provided within the hollow channel 5. A water outlet hole 9 is provided at the bottom of the hollow channel 5, communicating with the water channel 2, for passing a pipe connected to the water outlet of the water pump 8. Doors 10 are provided at the entrance and exit of the hollow channel 5, which is formed by the multiple sections of the wall 1 connected together, to seal the hollow channel 5.

[0049] Example 2

[0050] like Figures 1 to 6 、 Figure 8As shown, a permeable reaction wall device for acidic mineral water treatment is composed of multiple wall sections 1 connected in parallel. A caulking layer 13 is provided between the connecting gaps of the multiple wall sections 1 to maintain continuity between adjacent wall sections 1. Connection holes 11 are provided at the edges of the wall sections 1, and bolts are installed in the connection holes 11. Metal connecting plates 12 are installed on the bolts on adjacent wall sections 1 to fix the adjacent wall sections 1. An inverted trapezoidal water channel 2 is provided in the middle of the wall section 1. Several slots 3 are evenly arranged on the wall within the water channel 2. The upper ends of the slots 3 are tilted backward, and filter plates 4 are movably installed in the slots 3. The filter plates 4 are composed of a central plate-shaped filler layer 14 and a filter mesh 15 wrapped around the outer side of the plate-shaped filler layer 14. Hollow channels 5 are provided in the walls on both sides of the water channel 2. A concentration detector 6 is installed within the hollow channel 5. A diversion hole 7 is provided at the bottom of the hollow channel 5, communicating with the water channel 2. This hole is used to pass a pipe through the water channel 2 and transport the water in the water channel 2 to the concentration detector 6. A water pump 8 is also provided within the hollow channel 5. A water outlet hole 9 is provided at the bottom of the hollow channel 5, communicating with the water channel 2, for passing a pipe connected to the water outlet of the water pump 8. Doors 10 are provided at the entrance and exit of the hollow channel 5, which is formed by the multiple sections of the wall 1 connected together, to seal the hollow channel 5.

[0051] In the above embodiment, the connection mode between the multiple sections of the wall 1 can also be one of stacking up and down or any combination of parallel connection, series connection and stacking up and down.

[0052] Example 3

[0053] Fly ash was purchased from Lanke Water Purification Plant; nano-ferroferric oxide was purchased from Nangong Jingrui Alloy Products Co., Ltd.

[0054] A packing layer for a permeable reaction wall device used for acidic mineral water treatment, wherein the packing layer comprises a composite packing composed of fly ash, nano-ferroferric oxide and quartz sand in a mass ratio of 8:0.5 to 2:4, and is applied to a plate-shaped packing layer 14.

[0055] Table 4.3

[0056] Column number Filling Filling ratio Column length ratio 5 Fly ash: activated carbon 6g:6g 4cm:5cm 6 <![CDATA[Fly ash, nano-Fe3O4, quartz sand (uniformly mixed)]]> 8g:0.5g:4g 9cm 7 <![CDATA[Fly ash, nano-Fe3O4, quartz sand (uniformly mixed)]]> 8g:1g:4g 9cm 8 <![CDATA[Fly ash, nano-Fe3O4, quartz sand (uniformly mixed)]]> 8g:2g:4g 9cm

[0057] Depend on Figures 9-12 From the bar chart we can conclude that:

[0058] (1) By comparing the effluent results of tubes 5, 6, 7, and 8 after 12 hours of reaction, it can be seen that the removal of NH4 + Except for Mn, the treatment effect of fly ash mixed with nano-ferroferric oxide on acid mine water is better than that of fly ash mixed with coal-based activated carbon (6g:6g).

[0059] (2) According to the preliminary test results, fly ash and coal-based activated carbon (6g:6g) evenly mixed to reduce SO4 2- The removal rate of NH4 + The removal rate of Cu is 96%, the removal rate of Mn is 98%, the removal rate of Zn is 99%, and the removal rate of Ga is 98%. 2+ The removal rate of Mg is about 30%, while the removal rate of 2+ The removal rate is only 6%. Compared with the preliminary test results of the adsorption performance of a single filler, it can be seen that the fly ash and coal-based activated carbon mixed evenly as a reflective filler have a good removal effect on both heavy metals and NH4 + 、SO4 2- The removal effect is better than that of using coal-based activated carbon alone;

[0060] (3) By comparing the effluent results after 12 h of reaction between fly ash and nano-ferroferric oxide mixture (6, 7, 8 tubes) and single fly ash as filler, it can be seen that fly ash and nano-ferroferric oxide mixture (6, 7, 8 tubes) as filler has a negative effect on other heavy metals, heavy metal ions and NH4 + 、SO4 2- The treatment efficiency is higher than that of fly ash as a single filler;

[0061] (4) By comparing the effluent results of fly ash and nano-ferroferric oxide mixed in different proportions (tubes 6, 7, and 8) as fillers for 12 hours, it can be preliminarily concluded that when fly ash and nano-ferroferric oxide are evenly mixed in a ratio of 8g:1g, the NH4 + , Cu, Zn, Mn, and Fe have the highest removal efficiency, and NH4 + The removal rate of Cu is 98.6%, the removal rate of Mn is 98.2%, the removal rate of Zn is 99%, and the removal rate of Fe is 12%. 3+ Almost all of the Fe 2+ The removal rate of Ga 2+ and Mg 2+ For example, when fly ash and nano-ferroferric oxide are evenly mixed in a ratio of 8g:2g, the best treatment effect is 38% and 26.6%.

[0062] Composite filler durability test

[0063] The durability test was conducted on a filler made by mixing fly ash and nano-ferroferric oxide in a ratio of 8g:1g to test the adsorption performance of the filler.

[0064] The materials and methods were the same as above, but the reaction time was extended to 60 h. The results were as follows: Figure 13The change of the removal rate of heavy metals Cu, Zn and Mn with time shows that the removal effect of fly ash and nano-ferroferric oxide as filler is the best at about 12 hours, all reaching more than 95%. Then, with the increase of reaction time, the removal efficiency gradually decreases. Among them, the removal effect of Cu is the best, and it is still 90% after 60 hours of reaction, which is similar to the removal effect of fly ash as a single filler, which may be related to the low concentration of Cu in acidic mineral water; the removal effect of Zn is second, and it is still about 70% after 60 hours of reaction, which is about 15% higher than that of single fly ash as filler; although the removal effect of Mn is relatively the worst, compared with single fly ash as filler, the durability and maximum removal rate are the most enhanced, indicating that the use of nano-ferroferric oxide has a great effect on the removal of Mn.

[0065] Example 4

[0066] The acid mine seepage point of the red clay rock coal mine in Xiaogou Village, Yangquan Mining Area, and after on-site investigation, three sampling points were set up, located next to Yulin Nao upstream of Shandi River (H1), about 1 km before the acid mine water seepage (H2) and about 1 km after the acid mine water seepage (H3). Among them, H1 is located next to Yulin Nao Village upstream of Shandi River. It is close to the source of Shandi River and there is no pollution source nearby. The water quality is good and it can be used as a background point; H2 is about 1 km upstream of the Xiaogou acid mine water seepage point. Neutral mine water discharged from Yuejin Coal Mine flows in here. Neutral mine water basically does not contain pollutants, so the impact on the water quality of Shandi River is relatively slight. It can be used as a control point. H3 is about 1 km downstream of the Xiaogou acid mine water seepage point. At this time, the acid mine water seeping from the Xiaogou acid mine water seepage point has been mixed into the Shandi River water. At this time, the pH of the water body is significantly reduced, the color becomes yellow-brown, and the water quality is seriously polluted. Figure 14 Schematic diagram of the sampling location at Shandi River.

[0067] Comparison of microbial community characteristics in water before and after treatment

[0068] Sample preparation: 500 mL each of water samples from the Xiaogou acid mine water seepage point in Yangquan in July 2019, water samples after 12 hours of fly ash treatment, and water samples from various sampling points in Shandi River were collected. The filtrates were collected and all filtered through a 0.22 μm microporous filter membrane under vacuum filtration. The filter membrane enriched with bacterial samples was transferred to a centrifuge tube sterilized with high-pressure steam. The centrifuge tube was sealed and stored in an ice box and sent to Shanghai Meiji Biomedical Technology Co., Ltd. for testing. Separately, 500 mL each of water samples before and after treatment were collected, and a filtration apparatus was assembled. The water samples were filtered through a 0.22 μm microporous filter membrane. The filter membrane enriched with bacterial samples was transferred to a centrifuge tube sterilized with high-pressure steam. The centrifuge tube was stored in a -80°C freezer for scanning electron microscopy sample preparation.

[0069] High-throughput sequencing: DNA was extracted and amplified from water samples by Shanghai Meiji Biopharmaceutical Technology Co., Ltd., followed by sequencing using the Illumina Miseq PE300 platform (Shanghai Meiji Biopharmaceutical Technology Co., Ltd.). Sequencing data were processed and assembled using FLASH software. Sequences were clustered into OTUs at 97% similarity using UPARSE software (version 7.1), and singleton sequences and chimeras were removed during the clustering process. Each sequence was annotated with species classification using RDPclassifier and aligned to the Silva database (SSU123), with an alignment threshold of 70%.

[0070] Bacterial activity test: Most indigenous microorganisms in acidic mineral water can oxidize Fe 2+ , Determining the overall ferrous oxidation activity of bacteria in water can be used to approximate the overall activity of bacteria in the water sample. The analysis is performed using the potassium dichromate titration method, with the following steps:

[0071] (1) Prepare 9K medium A according to the formula, adjust the pH to 3 with 1:1 sulfuric acid, prepare the cleaned equipment and sterilize it with medium A under high pressure. Then prepare 9K medium B according to the formula, filter it through a 0.22 um microporous filter membrane after sterilization, and mix liquid A and liquid B to make 9K medium.

[0072] (2) Use a measuring cylinder to measure 90 mL of the mixed 9k culture medium and place it in a 250 mL conical flask. Use a sterilized pipette to transfer 10 mL of the water sample before and after treatment into the conical flask. These are the bacterial culture solutions for each sample point. The blank control culture solution is prepared simultaneously by replacing the water sample with 10 mL of sterile water.

[0073] (3) Determination of the initial Fe content of the culture medium at each sample point using potassium dichromate titration 2+ The concentration should be recorded in the experimental notebook. Titration method: Take 2 mL of culture medium in a conical flask, add 10 mL of sulfuric acid and phosphoric acid, add 2-3 drops of sodium diphenylamine sulfonate indicator, and use potassium dichromate solution to titrate until the solution suddenly turns purple. Record the volume of potassium dichromate solution consumed.

[0074] (4) Place each culture medium in a bacterial incubator and set the constant temperature at 30°C for 7 days. After 7 days, take out the culture medium and measure the Fe content in each culture medium again according to step 7. 2+ The concentration was recorded in the experimental notebook, and the bacterial activity was expressed as the oxidation rate of ferrous ions by bacteria after 7 days of culture.

[0075] (5) Calculation of results:

[0076] Calculate the ferrous iron oxidation rate u of bacteria in the culture solution of each sample point according to the following formula:

[0077] u = ( [ Fe 2+ ]0-[ Fe 2+ ]) / ([ Fe 2+ ] 空白 ) × 100%. Among them, [Fe 2+ ] 空白 is the ferrous ion concentration of the blank culture medium after one week of synchronous culture, [Fe 2+ ]0 is the initial concentration before culture, [Fe 2+ ] is the concentration after one week of culture.

[0078] Scanning electron microscopy analysis: Scanning electron microscopy provides a direct visualization of bacterial abundance and morphology in water samples before and after treatment. X-ray energy dispersive spectroscopy analysis was also performed. The specific steps were as follows: 500 mL of each water sample was collected before and after treatment. A filtration apparatus was assembled and the sample was filtered through a 0.22 μm microporous filter membrane. The filter membrane was removed and placed in a beaker. 10 mL of secondary water was added and ultrasonicated for 10 minutes. After sonication, the filter membrane was removed. The solution in the beaker constituted the bacterial enrichment solution. A certain amount of the bacterial enrichment solution was centrifuged at 8000 rpm for 3–5 minutes, and the supernatant discarded. The sample was fixed with 2%–4% 2.5% glutaraldehyde and refrigerated for 1–2 hours. The sample was then washed twice with phosphate buffered saline. The sample was then soaked in 50%, 70%, and 90% ethanol for approximately 8 minutes each, followed by dehydration with 100% ethanol for 15 minutes. The sample was then replaced with isoamyl acetate twice, 20 minutes each time. The sample was dried in a constant temperature drying oven at 30°C for 24 hours, and then gold-sprayed.

[0079] result

[0080] Changes in bacterial community diversity

[0081] Microorganisms play a crucial role in the dissolution of pyrite and the formation of acidic mineral water. The bacterial diversity in water bodies can reflect the ecological function of the water body, further reflecting the impact of acidic mineral water infiltration on downstream mountain river water. The Goods-coverage rate of each sample library was greater than 99.5%, indicating that the sample results were usable. Alpha diversity refers to the diversity of microbial communities within a specific ecosystem, and the number of OTUs can reflect the number of species in the bacterial community within the water body. The Shannon index and Simpson index can be used to measure sample diversity. The Ace index is used to measure species richness.

[0082] Bacterial community diversity index in samples of tacrolimus mineral water and mountain river

[0083] sample Number of OTUs Shannon Index Ace Index Coverage AMD 218 2.285 247.13 99.89% H1 637 3.299 873 99.5% H2 321 3.714 391.74 99.95% H3 474 4.656 478.45 99.95%

[0084] The species composition of bacterial communities can deeply reflect the overall situation of bacterial communities. Since there is little taxonomic information on bacterial species at the species level, it is mainly discussed at the genus level, such as Figure 15 Bacterial community distribution at various sampling points at the genus level.

[0085] Acidithiobacillus was the most dominant genus in the bacterial community of acid mine water, accounting for 32.90% of the total abundance. Acidithiobacillus ferrooxidans was the dominant species within the genus. This Gram-negative bacterium is chemoautotrophic, aerobic, acidophilic, and adaptable to mesophilic environments. It is widely found in acid mine water and acidic environments containing iron or sulfur. Acidiphilium was the second most dominant genus in the AMD, accounting for 24.5% of the total abundance. This bacterium has an optimal growth temperature of 29-33°C and a pH of 3.0-4.0, and has consistently been the dominant species in our group's recent studies of this AMD. Acidibacillus was the third most dominant genus in the AMD, accounting for 15.6% of the total abundance. Ferrovum was the third most dominant genus in the AMD, accounting for 8.1% of the total abundance. It is an inorganic chemoautotroph, acidophilic, and can oxidize Fe. 2+ .

[0086] In the water body at the source of the Shandi River, sampling point H1, Sphingomonas and Acinetobacter were the dominant members of the community, while the abundance of other genera was extremely low, resulting in a simple bacterial community composition. In the water body H2 in the middle reaches, the bacterial community underwent significant changes. Sphingomonas almost disappeared, and Enterobacter became the new dominant genus with an abundance of 19.3%, indicating that the water body was affected by human and livestock activities and agricultural production. Acinetobacter became the second dominant genus with an abundance of 14.7%. Rhodococcus had a moderate abundance and showed biodegradation and decontamination capabilities. The planktonic bacteria Limnohabitans and the microorganism Polynucleobacter, which are symbiotic microorganisms in ciliates, had low abundances of 5.15% and 3.59%, respectively. They are common microorganisms in natural freshwater bodies. After the infiltration of acidic mineral water, the bacterial community structure in the mountain river water sampling point H3 showed completely different characteristics from the upstream and middle reaches. The abundance of facultative anaerobic bacteria and anaerobic bacteria Escherichia-shigella, Bacterodies, and Paenibacillus increased significantly, and the total abundance reached about 20%, indicating that the dissolved oxygen in the water body was consumed in large quantities, reflecting that the organic pollution in the water body was relatively serious. It is worth noting that the appearance of a small number of pathogenic bacteria such as Fusobacterium, Escherichia-shigella, and Hepatobiliary bacteria in the water body also indicates that the water quality has deteriorated seriously after being polluted by acidic mineral water. At the same time, a small amount of Acidithiobacillus (acidophilic thiobacillus), Acidiphilium (acidophilic chemoheterotrophic bacteria) and ferrovum appeared in the water body, indicating that the water body was seriously affected by the acidic mineral water.

[0087] Analysis of the results of ferrous oxidizing bacteria activity test

[0088] From July 2019 to November 2019, the bacterial activity in each water sample generally showed a gradually declining trend. The bacterial activity was generally the highest in July 2019. This may be related to the fact that the water environment in June and July in summer is most suitable for bacteria to catalyze ferrous oxidation reactions. As the weather turns cooler, the bacterial ferrous oxidation activity also gradually decreases; the bacterial activity change trends of AMD and H3 water samples are similar, and are significantly higher than those of H1 and H2, indicating that there is a certain proportion of iron-sulfur oxidizing bacteria in H3; the activity of H1 and H2 is always low, both below 6%. This part of the activity is likely due to chemical oxidation, so H1 and H2 may not contain iron-sulfur oxidizing bacteria.

[0089] The activity of iron-oxidizing bacteria in the treated water sample dropped to 12.3%. Although there was still a certain proportion of iron-sulfur oxidizing bacteria, the iron-oxidizing bacteria in the water had been greatly degraded compared with the H3 water sample after acid mine water infiltration, indicating that reducing the activity of iron-oxidizing bacteria has a great impact on improving water quality.

[0090] SEM results analysis

[0091] The results of sample 1 and sample 2 observed by JSM-ITHR scanning electron microscope are as follows Figure 17 、 18 As shown ( Figure 17 、 Figure 18 The magnification is 40 times): Under the same magnification, Figure 17 and Figure 18 By comparison, it can be found that there are a large number of rod-shaped bacteria in sample one, while there are obviously fewer rod-shaped bacteria in sample two. Through bacterial technology experiments, bacterial activity experiments, and high-throughput sequencing technology to analyze the bacterial community at the acid mine water seepage point in Xiaogou Village, Yangquan, it can be found that Thiobacillus ferrooxidans (Af bacteria) is the most important dominant bacteria, so it can be further determined that the microorganism in the picture is Thiobacillus ferrooxidans. By using fly ash as filler and self-designed white PVC pipe plastic cylinder as a reactor, the number of Thiobacillus ferrooxidans in the acid mine water was significantly reduced. It can be concluded that reducing the number of Thiobacillus ferrooxidans has a great influence on improving the quality of acid mine water. In order to further understand it, we then selected Figure 17 Figure 18 Each of the rod-shaped bacteria in the sample is scanned to obtain the X-ray energy spectrum, such as Figure 19 The X-ray energy spectrum analysis diagram of the samples before and after acid mine water treatment is shown in the figure.

[0092] From the X-ray energy spectra of the samples before and after treatment, it can be clearly found that the element with the highest concentration in the acid mine water is Fe. After treatment, the Fe element is almost completely removed, while the main element C in fly ash causes a significant increase in the C element in the treated water sample, indicating that fly ash has a strong ability to remove Fe.

[0093] The community composition of acidic mineral water is relatively simple, primarily composed of Acidithiobacillus, Acidiphilium, Acidibacillus, and Ferrovum. Acidithiobacillus ferrooxidans is the most abundant species within the Acidithiobacillus family and is a key microorganism controlling the rate of acidic mineral water production. The species composition of H1 at the source of the Shandi River and H2, which is affected by neutral mineral water, is relatively similar. However, H3, which has been infiltrated by acidic mineral water, exhibits significant changes in species composition. The presence of facultative anaerobes, anaerobes, enterobacteria, and pathogens indicates significant depletion of dissolved oxygen, severe organic pollution, and deterioration of water quality. Small amounts of Acidithiobacillus and Acidiphilium have also appeared in the water.

[0094] Ferrous oxidizing bacteria activity testing and scanning electron microscopy analysis both showed a significant reduction in the number of iron-oxidizing bacteria in the treated water samples, demonstrating that reducing the number of iron-oxidizing bacteria has a significant impact on improving the quality of acid mine water. X-ray spectra of samples before and after treatment clearly show that the most concentrated element in the acid mine water is iron (Fe). Treatment almost completely removes this element, demonstrating the fly ash's strong ability to remove Fe.

[0095] Any matters not described in detail in this specification are prior art known to those skilled in the art. Although the above description of the present invention is based on specific embodiments to facilitate understanding of the present invention by those skilled in the art, it should be understood that the present invention is not limited to the specific embodiments. As long as various variations are within the spirit and scope of the present invention as defined and determined, they will be readily apparent to those skilled in the art, and all inventions utilizing the present invention are protected.

Claims

1. A permeable reaction wall device for acidic mineral water treatment, characterized by: It is composed of multiple wall sections (1) connected together, an inverted ladder-shaped water channel (2) is provided in the middle of the wall (1), a plurality of slots (3) are evenly provided on the wall inside the water channel (2), and a filter plate (4) is movably provided in the slot (3); The upper end of the slot (3) is tilted backwards to enable the filter plate (4) to be placed at an angle; Hollow channels (5) are provided in the walls on both sides of the water channel (2), a concentration detector (6) is provided in the hollow channel (5), and a guide hole (7) in communication with the water channel (2) is provided at the bottom of the hollow channel (5) for passing through a pipeline to transport the water in the water channel (2) to the concentration detector (6); A water pump (8) is also provided in the hollow channel (5), and a water outlet hole (9) communicating with the water channel (2) is also provided at the bottom of the hollow channel (5) for passing a pipe connected to the water outlet end of the water pump (8); The filter plate (4) is composed of a middle plate-shaped filler layer (14) and a filter mesh (15) wrapped around the outer side of the plate-shaped filler layer (14); The filler in the plate-shaped filler layer (14) is composed of fly ash, nano-ferroferric oxide and quartz sand in a mass ratio of 8:0.5 to 2:

4.

2. The permeable reaction wall device for acidic mine water treatment according to claim 1, characterized in that: The connection mode between the multiple sections of the wall (1) can be one of parallel connection, series connection, stacking up and down, or any combination thereof.

3. The permeable reaction wall device for acidic mine water treatment according to claim 2, characterized in that: A caulking agent layer (13) is provided between the connecting gaps of the multiple sections of the wall (1) to maintain the continuity between adjacent walls (1).

4. The permeable reaction wall device for acidic mine water treatment according to claim 3, characterized in that: Opening and closing doors (10) are provided at the entrance and exit of the hollow passage (5) formed by the wall (1) connected together in multiple sections, so as to achieve the closure of the hollow passage (5).

5. A filler for use in the permeable reaction wall device for acidic mineral water treatment according to claim 1, characterized in that: The filler is composed of fly ash, nano-ferroferric oxide and quartz sand in a mass ratio of 8:0.5 to 2:4, and is applied to the plate-shaped filler layer (14).

6. An application of the permeable reaction wall device for acidic mine water treatment according to claim 1, characterized in that: Used to treat acid mine water pollution.

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