CN114262059A - Urban tail water purification system of vertical flow constructed wetland - Google Patents
Urban tail water purification system of vertical flow constructed wetland Download PDFInfo
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- CN114262059A CN114262059A CN202111573311.3A CN202111573311A CN114262059A CN 114262059 A CN114262059 A CN 114262059A CN 202111573311 A CN202111573311 A CN 202111573311A CN 114262059 A CN114262059 A CN 114262059A
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Images
Abstract
The invention provides a city tail water purification system of a vertical flow artificial wetland, which comprises: the water body purification substrate and the coarse sand are sequentially covered on the upper surface of the crushed stone; wherein the water body purification substrate is a mixture of biochar and basalt macadam; the mass ratio of the biochar to the basalt broken stone is (2.21-3.79): 100 with the grain diameters of 2-8mm and 2-10mm respectively; the particle size of the crushed stone is 10-20 mm; the grain diameter of the coarse sand is 0.5-2 mm. The invention improves the application range of the straw biochar, avoids the adverse effect of substrate blockage, obtains the optimal application condition of the straw biochar, and has important significance for promoting the application of the straw biochar in the artificial wetland and improving the urban tail water purification effect of the artificial wetland.
Description
Technical Field
The invention relates to the technical field of sewage purification treatment, in particular to a vertical flow constructed wetland urban tail water purification system.
Background
The artificial wetland is an important ecological sewage treatment method, and has obvious advantages in treating dispersed community sewage, rural domestic sewage and urban tail water. The urban tail water has large production amount and nitrogen and phosphorus concentration higher than that of the surface water body, and the direct discharge can aggravate the pollution of the water body. The artificial wetland has the advantages of low cost, high efficiency, ecological safety and the like in treating urban tail water. The artificial wetland purification process of pollutants mainly comprises three parts of filtration adsorption and ion exchange of a matrix, plant absorption and microbial decomposition, wherein the matrix has a promoting effect on the plant absorption and the microbial decomposition. As a carrier of wetland plants and microorganisms, the adsorption and ion exchange effects of the matrix have important significance for removing pollutants in sewage.
The artificial wetland substrate is divided into a natural substrate, a waste utilization substrate and an artificial substrate according to material sources. The research on artificial matrices has been developed more rapidly, since natural matrices have a relatively weak adsorption capacity and waste-use matrices risk the introduction of contaminants.
The biochar applied to the current artificial wetland comprises coconut shells, walnut shells, reed, bamboo charcoal, plant straws and the like as raw materials, wherein the plant straw biochar is less in application, and the plant straw biochar is mainly used for preparing carbon-based fertilizers. Therefore, the application of the biochar in the constructed wetland matrix has great uncertainty. The vertical flow artificial wetland occupies a small area, has high purification efficiency on pollutants, and has stronger treatment capacity than the horizontal flow artificial wetland. But the vertical flow constructed wetland is easier to block.
Therefore, how to apply the biochar to a vertical flow artificial wetland purification system is a technical problem which needs to be solved urgently by the technical personnel in the field.
Disclosure of Invention
In view of the above, the invention provides a vertical flow constructed wetland purification system, which improves the application range of the straw biochar, avoids the adverse effect of substrate blockage, obtains the optimal application condition of the straw biochar, and has important significance for promoting the application of the straw biochar in the constructed wetland and improving the purification effect of the constructed wetland urban tail water.
In order to achieve the above effects, the present invention provides a vertical flow constructed wetland purification system, a vertical flow constructed wetland urban tail water purification system, comprising: the water body purification substrate and the coarse sand are sequentially covered on the upper surface of the crushed stone;
wherein the water body purification substrate is a mixture of biochar and basalt macadam;
the mass ratio of the biochar to the basalt broken stone is (2.21-3.79): 100.
preferably, the biochar is unmodified straw biochar, and the particle size of the biochar is 2-8 mm.
Further, the biochar is prepared from crop straw raw materials at the temperature of 450 +/-25 ℃ (N)2) The temperature condition, the heating rate of 10 ℃/min and the pyrolysis time of 2.0 hours. The prepared straw biochar passes through a sieve with the aperture of 2mm, and the straw biochar on the sieve is reserved; and sieving the straw by using a sieve with the aperture of 8mm, and reserving the straw biochar under the sieve.
Further crushing the straw biochar on the screen, screening again, and finally reserving the straw biochar with the diameter of 2-8 mm. And (3) soaking the screened biochar, washing the biochar for 3-5 times by using water until no obvious ash can be seen in the cleaning water body, and cleaning the biochar for 10 minutes by using an ultrasonic cleaning machine. And drying the cleaned biochar to constant weight by using an oven to obtain the straw biochar.
The beneficial effects of adopting the above technical scheme at least include: because the particle size of the straw biochar is too small, the permeability coefficient is small, and blockage is easily formed, although the permeability coefficient is improved to a certain extent in a certain particle size range, blockage is still easily formed after long-term operation, but the particle size is too large, and the removal rate of pollutants is reduced, so that in order to prevent blockage and ensure the removal efficiency of pollutants, and simultaneously fully utilize the straw biochar to achieve the purification effect, the technical effect which is not intended can be achieved only by a proper particle size range and a proper proportion relation.
Preferably, the biochar is modified straw biochar, and the particle size of the biochar is 2-8 mm.
Wherein the modified straw biochar is selected from potassium permanganate straw biochar, sodium hydroxide modified biochar or composite modified biochar of potassium permanganate and sodium hydroxide.
The beneficial effects of adopting the above technical scheme at least include: the system mainly removes nitrogen and phosphorus in the urban tail water through adsorption and ion exchange precipitation, and besides, the straw biochar is used as an artificial wetland substrate and a supplementary carbon source and can promote microbial denitrification and plant dephosphorization; the modified straw biochar is further adopted, and compared with unmodified straw biochar, the modified straw biochar improves the specific surface area and pore volume of the unmodified straw biochar, increases the number of functional groups and the like, and further can further improve the adsorption capacity and ion exchange capacity of the biochar; provides a theoretical basis for the subsequent development of the research on the purification of the modified biochar as the artificial wetland substrate for the urban tail water.
Preferably, the particle size of the crushed stone is 10-20 mm.
The beneficial effects of adopting the above technical scheme at least include: the constructed wetland system is prevented from being blocked by carbon powder generated by the destruction of the biochar in the construction process along with the flow of water, and the biochar in the crushed stone can be biodegraded to relieve the blockage.
Preferably, the basalt broken stone is slightly weathered basalt broken stone, and the particle size is 2-10 mm.
The beneficial effects of adopting the above technical scheme at least include: the requirement of the permeability of the constructed wetland substrate is met, and meanwhile, a larger contact area with the water body is obtained, and the purification effect is improved.
Preferably, the particle size of the coarse sand is 0.5-2 mm.
The beneficial effects of adopting the above technical scheme at least include: promote the growth of plants and reduce the washing of the biochar by water.
Preferably, the ecological system at least comprises acorus calamus, the plant height of the acorus calamus is 320mm in 300-250 plants/m in the planting density of 200-250 plants/m2。
The beneficial effects of adopting the above technical scheme at least include: the system adopts the acorus calamus with strong capability of removing nitrogen and phosphorus, and can further assist the unmodified/modified straw biochar in removing the nitrogen and phosphorus; meanwhile, under the condition of plants, dissolved oxygen in the urban tail water is consumed by nitration reaction, and the denitrification effect is further improved by oxygenation and aeration.
And the modified straw biochar has the advantages of increasing the specific surface area and pore volume, serving as a carrier of wetland plants and microorganisms, promoting the growth of the microorganisms, promoting the nitrification and denitrification of an artificial wetland system, and further improving the purification effect.
Preferably, the removal rate of TN (total nitrogen) by the urban tail water purification system of the vertical flow constructed wetland>NH4 +-N and COD, and TN had an average removal rate of 91.91% and NH4 +The average removal rate of-N was 88.14%, and the average removal rate of COD was 73.04%.
Preferably, the average removal rate of the vertical flow constructed wetland urban tail water purification system TN is 89.92%, and NH is4 +Average removal of-N86.58%, average removal of COD 88.39%, and average removal of NO3 -The average removal of-N was 91.24%.
Preferably, the modified straw biochar is selected from sodium hydroxide modified biochar, so that the average TN removal rate of the vertical flow constructed wetland urban tail water purification system is 88.60%, and NH content is4 +Average removal of-N95.21%, NO3 -The average removal of-N was 89.10%.
In summary, the present invention has at least the following advantages:
1) the purification mechanism of nitrogen and phosphorus in the urban tail water is explored by adding different straw biochar, and the removal rate of nitrogen and phosphorus is improved as the addition amount of the biochar is increased in a certain proportion range by the straw biochar and the basalt macadam; and the biological carbon matrix promotes plant growth and nitrification and denitrification reactions of the artificial wetland system, and improves the purification effect of the artificial wetland on the urban tail water.
2) Simultaneously, when the adding mass ratio of the straw biochar is 2.95%, the purification effect of urban tail water is relatively good, and the overall NH ratio is improved under the combined action of the plant calamus flavus and the straw biochar4 +-N、TN、NO3 --removal of N and TP.
3) The invention also provides a purification mechanism of nitrogen and phosphorus in the urban tail water by the biochar substrate under different modification conditions, and sodium hydroxide is modifiedBiochar substrate, adsorption and NH4 +Enhances the removal of nitrogen under the action of cation exchange, can promote the plant growth and the nitrification and denitrification reactions of the artificial wetland system, and treats NH under the combined action of plants and matrix4 +-N、TN、NO3 -The removal rate of-N is obviously improved.
4) Meanwhile, the specific surface area and the pore volume of the modified straw biochar are increased, the adsorption performance can be improved, the adsorption of phosphorus is improved due to the increase of the average pore diameter and the action of manganese oxide attached to the surface of the biochar, and the removal rate of TP in urban tail water is improved under the combined action of a matrix and plants.
5) The modified straw biochar can promote the nitrification of the artificial wetland system to increase oxygen consumption, the oxygen consumption is increased along with the increase of the operation time of the artificial wetland, and the appropriate oxygenation and aeration is favorable for improving the nitrification reaction.
Drawings
In order to more clearly illustrate the technical solutions in the embodiments of the present invention, the drawings needed to be used in the embodiments will be briefly described below, and it is apparent that the drawings in the following description are only embodiments of the present invention, and it is obvious for those skilled in the art that other drawings can be obtained according to the provided drawings without creative efforts.
FIG. 1 is a drawing showing NH in city tail water added with different amounts of straw biochar in examples 2-74 +-N processing results.
FIG. 2 is a graph showing TN treatment results of different amounts of straw biochar added to city tail water in examples 2-7.
FIG. 3 is a graph showing NH in city tail water added with different amounts of biochar from straw under plant conditions in examples 8-134 +-N processing results.
FIG. 4 is a graph showing TN treatment results of different amounts of straw biochar added to urban tail water under the plant conditions in examples 8 to 13.
FIG. 5 is a graph showing N in urban tail water added with biochar from different straws under the condition of plants in examples 8-13O3 --N processing results.
FIG. 6 is a graph showing the amount of biochar added to NH in city tail water in the presence and absence of plants according to examples 2-134 +-N treatment result alignment graph.
FIG. 7 is a graph showing the comparison of TN treatment results of urban tail water with different amounts of straw biochar added under the conditions of plants and no plants in examples 2-13.
FIG. 8 is a graph showing the results of COD treatment in municipal wastewater by adding different amounts of biochar from straw in examples 2 to 7.
FIG. 9 is a graph showing the results of COD treatment of municipal wastewater by the addition of biochar from different stalks under the condition of plants in examples 8 to 13.
FIG. 10 is a graph showing NH in city tail water added with different modified straw biochar amounts in examples 2 and 14-174 +-N processing results.
FIG. 11 is a graph showing TN treatment results of examples 2 and 14 to 17 on municipal tail water at different modified straw biochar addition levels.
FIG. 12 is a graph showing NH in city tail water added with different modified straw biochar amounts in examples 12 and 18-21 under the condition of plants4 +-N processing results.
FIG. 13 is a graph showing TN treatment results of different modified straw biochar addition amounts in urban tail water under the condition of plants in examples 12 and 18-21.
FIG. 14 is a graph showing the addition amount of different modified straw biochar to NO in urban tail water under the condition of plants in examples 12 and 18 to 213 --N processing results.
FIG. 15 is a graph showing the comparison of TN treatment results of different modified straw biochar addition amounts in urban tail water under the conditions of plants and no plants in examples 2, 12 and 14-21.
FIG. 16 is a diagram illustrating a mechanism for removing nitrogen from city tail water according to an embodiment of the present invention.
Detailed Description
The technical solutions in the embodiments of the present invention will be clearly and completely described below with reference to the drawings in the embodiments of the present invention, and it is obvious that the described embodiments are only a part of the embodiments of the present invention, and not all of the embodiments. All other embodiments, which can be derived by a person skilled in the art from the embodiments given herein without making any creative effort, shall fall within the protection scope of the present invention.
Example 1
The embodiment provides a city tail water purification system of a vertical flow artificial wetland, which comprises an artificial wetland matrix column, wherein the height of the artificial wetland matrix column is 450mm, and the diameter of the artificial wetland matrix column is 160mm (inner diameter);
the height of the water body purification substrate is 300mm, meanwhile, 50mm of broken stones with the height and the grain size of 10-20mm are arranged at the bottom, and the water body purification substrate is laid on the broken stones;
coarse sand with the height of 50mm is arranged at the top of the water body purification substrate, and the particle size of the coarse sand is 0.5-2 mm.
Wherein the water body purification substrate is a mixture of biochar and basalt macadam, and the mass ratio is (2.21-3.79): 100.
in order to further optimize the technical scheme, the biochar is straw biochar.
In order to further optimize the technical scheme, the basalt broken stone is slightly weathered basalt broken stone, and the grain size is 2-10 mm.
Example 2
On the basis of the embodiment 1, the water body purification substrate is not added with biochar and is completely composed of basalt macadam.
Example 3
On the basis of the embodiment 1, the biochar is unmodified straw biochar, and the mass ratio of the biochar to the basalt crushed stone is 0.98 percent respectively.
Example 4
On the basis of the embodiment 1, the biochar is unmodified straw biochar, and the mass ratio of the biochar to the basalt crushed stone is 1.56%.
Example 5
On the basis of the embodiment 1, the biochar is unmodified straw biochar, and the mass ratio of the biochar to the basalt crushed stone is 2.21%.
Example 6
On the basis of the embodiment 1, the biochar is unmodified straw biochar, and the mass ratio of the biochar to the basalt crushed stone is 2.95%.
Example 7
On the basis of the embodiment 1, the biochar is unmodified straw biochar, and the mass ratio of the biochar to the basalt crushed stone is 3.79%.
Example 8
On the basis of example 2, yellow flag is introduced, the height of the yellow flag is 300mm, and 4 plants are planted.
Example 9
On the basis of example 3, yellow flag is introduced, the height of the yellow flag is 300mm, and 4 plants are planted.
Example 10
On the basis of example 4, yellow flag is introduced, the height of the yellow flag is 300mm, and 4 plants are planted.
Example 11
On the basis of example 5, yellow flag is introduced, the height of the yellow flag is 300mm, and 4 plants are planted.
Example 12
On the basis of example 6, yellow flag is introduced, the height of the yellow flag is 300mm, and 4 plants are planted.
Example 13
On the basis of example 7, yellow flag is introduced, the height of the yellow flag is 300mm, and 4 plants are planted.
Data test one
The system according to examples 2-13, wherein the COD concentration was 50mg/L, NH, treated the same batch of municipal tail water4 +The concentration of N is 5.0mg/L and the concentration of TN is 15.0 mg/L; the concentration of TP is considered to be about 0.5mg/L to 0.8 mg/L. The residence time of the urban tail water is 3d, and the hydraulic load is 0.055m3·(m2·d)-1. The preparation is carried out indoors at the room temperature of 20-30 ℃; the water sampling method is a mixed water sample of water in the middle and the lower part of the artificial wetland matrix column, three water samples are taken each time, and the test equipment adopts a GL-900 multi-parameter water quality tester and a GL-25 intelligent digestion instrument for measurement. The Electrical Conductivity (EC) is measured byThe conductivity meter measures the water-distributed urban tail water before and after the artificial wetland treatment. Measuring Dissolved Oxygen (DO) by using a portable Dissolved oxygen analyzer, and measuring pH by using a desktop pH meter; NH was measured every 24 hours4 +And (4) measuring the concentrations of N, TN, TP and COD (chemical oxygen demand) for 8 times, and dynamically simulating the removal of pollutants by the artificial wetland.
Data processing: and simulating wetland degradation pollutants by adopting a first-stage kinetic equation and a second-stage reaction kinetic equation, and analyzing the degradation rule. The first order kinetic equation simulation is shown in equations 4-1 and 4-2, and the second order reaction kinetic equation is shown in equations 4-3 and 4-4.
In the formula CoutThe effluent concentration is mg/L; cinThe water inlet concentration is mg/L; t is the hydraulic retention time h of the system; k is a radical of25Is the volume rate constant (1/h) for contaminant removal at 25 deg.C, the experiment was performed at 25 deg.C, the rate constant kTIs to draw an In (C) line through experimentsout) T is determined by a relation curve;
is the half-life, h.
In addition to model processing, experimental data were analyzed using Microsoft Excel 2016, IBM SPSS Statistics 23.0, and Origin 2017 software from Microsoft corporation, 3 replicates of municipal tailwater removal indicators were measured, and the mean and standard deviation were calculated. Because the standard deviation of the conductivity is small, the drawing is difficult to embody. Comparative analysis was performed on the substrates of examples 8 to 13 and examples 2 to 7 for the purification of urban tail water from artificial wetlands.
Meanwhile, the biomass (fresh weight) of the plant is measured in each of examples 8 to 13, and part of leaves and roots are selected to measure the water content, the nitrogen content and the phosphorus content, and the dry weight of the plant is converted. Fresh weight is measured by removing water from the surface of the plant with filter paper. The dry weight is measured by deactivating enzymes at 105 deg.C for 30min in a drying oven, and then drying at 80 deg.C to constant weight. The measuring method of the nitrogen and the phosphorus of the plants comprises the following steps: grinding the dried plants into powder, weighing 0.5g of the powder, putting the powder into a digestion tube, collecting and digesting the powder, and determining the content of nitrogen and phosphorus.
Wherein, table 1 is a linear simulation result of a first-order reaction kinetic equation, and table 2 is a linear simulation result of a second-order reaction kinetic equation.
The test results are shown in fig. 1 to 8.
Wherein, as shown in fig. 1: examples for NH4 +The removal of N increased and then decreased, and after day 15, NH was adjusted for each example4 +The removal rate of-N is in a descending trend, which is mainly because the adsorption capacity of the straw biochar and the crushed stone is limited, and because the substrates gradually tend to be saturated in the purification process and the purification effect gradually decreases due to no microbial decomposition and transformation and no absorption of plants. Wherein the 1# experimental group is not added with straw biochar and is treated with NH after the 30 th day4 +The decrease in the purification rate of-N is most pronounced. This indicates that the crushed stone is in NH pairs compared with straw biochar4 +The adsorption, filtration and ion exchange of-N are more likely to enter saturation. The adsorptivity of the broken stone is obviously lower than that of the straw biochar, and the broken stone can easily enter a saturated state under the condition of the same concentration. Therefore, the NH of the artificial wetland is difficult to ensure only by the action of the substrate4 +-N long-term decontamination effect.
FIG. 2 shows: the removal rate of TN of examples 5 to 6 was substantially more than 80%. The removal rate of TN in the embodiment 2 is basically below 50%, and the removal rate of TN in the embodiment 3 is basically below 70%. Overall, the concentration of TN in each example tended to increase, and the removal rate tended to decrease. After day 33 both the increase in TN concentration and the decrease in removal rate were most pronounced.
The removal rate of TN in the embodiment 5 and the embodiment 7 is obviously higher, which shows that the purification effect of TN is obviously improved after the straw biochar is added into the artificial wetland substrate. The examples 2 to 4 had large fluctuation in the removal rate of TN, and the other examples had small fluctuation. This is mainly because examples 2-4 have a low content of biochar and their removal rates are greatly affected by external conditions. And the biochar added in the embodiments 5-7 is relatively more, the higher adsorptivity and higher filtering performance of the biochar improve the stability of the constructed wetland system in removing TN, and further reduce the fluctuation change of the purification rate of the constructed wetland.
FIG. 3 shows: after day 12, NH4 +The removal rate of-N was between 70 and 90%, and the removal rate tended to be steady after day 15 without decreasing tendency.
FIG. 4 shows: after day 15, the removal of TN was substantially between 70 and 90% except for examples 8 to 9, and the removal tended to be steady.
And NH4 +like-N, after introduction into plants, the TN concentration was higher for the first 15 days due to contaminants brought by the plant roots. TN removal rate after day 15 tended to be stable, indicating that after increasing the plants, the city tail water brought TN (NH) in the system4 +-N and NO3 -N) is partially absorbed by the plant and acts as a rhizosphere microorganism, supplementing the reduction in TN removal due to the progressive tendency of the matrix to saturate. In addition, denitrification significantly reduces NO3 -The concentration of N, and thus of TN.
FIG. 5 shows: examples 11-12 achieved removal rates of around 90% after day 12. Examples 8 to 9 on NO3 -The removal of-N is less effective. Examples are for NO as a whole3 -The removal rate of-N is on an increasing trend.
FIG. 6 shows: whether in the absence of plant conditions or in the presence of plant conditions, with the organismIncrease in carbon addition, NH4 +The removal rate of-N is on an increasing trend. Under the condition of no plant, the removal rate of the artificial wetland experimental group has small difference. The main reason is that the adsorption of the biological matrix is higher than that of the crushed stone, and the removal rate of ammonia nitrogen is improved along with the increase of the adding proportion of the biochar. Under the condition of plants, the addition of the straw biochar can improve the NH pair of the artificial wetland4 +And (4) removing the N, but the excessive addition of the biochar cannot obviously improve the ammonia nitrogen purification effect of the constructed wetland. This is probably because the plant growth rhizosphere microorganisms have limited carbon source requirements, while the excess biochar reduces the permeability of the constructed wetland to NH4 +The removal of-N has an adverse effect.
FIG. 7 shows: with the increase of the addition amount of the biochar, the difference between TN removal rates under the conditions of plants and non-plants is smaller and smaller, and the biochar can promote the plants to remove TN.
Fig. 8-9 show: compared with the condition without plants, the concentration of the urban tail water COD of the artificial wetland system of each experimental group is obviously reduced under the condition with plants, and the removal rate is obviously improved. The improvement of each example is about 10-15% after the artificial wetland system is introduced into the plants. The biological carbon can promote the removal of COD in a certain biological carbon adding proportion range under the plant growth condition. This is mainly because biochar can promote the growth and reproduction of plants and plant rhizosphere microorganisms, thereby improving the removal of COD. And by combining the linear fitting result of the first-order reaction kinetics, the removal efficiency of the artificial wetland system on COD is relatively high in a certain biochar adding range. The removal of COD is also influenced by factors such as the concentration of dissolved oxygen in the artificial wetland system, nitration reaction, denitrification and the like. The decomposition of the plants can release organic matters into the water body, and the influence on the COD concentration is large.
TABLE 1
TABLE 2
Example 14
On the basis of the embodiment 6, the biochar is sodium hydroxide modified straw biochar, and the mass ratio of the biochar to the basalt broken stone is 2.95%.
Example 15
On the basis of the embodiment 6, the biochar is potassium permanganate modified straw biochar, and the mass ratio of the biochar to the basalt macadam is 2.95%.
Example 16
On the basis of the embodiment 6, the biochar is freeze-thaw cycle modified straw biochar, and the mass ratio of the biochar to the basalt macadam is 2.95%.
Example 17
On the basis of the embodiment 6, the biochar is freeze-thaw cycle and sulfuric acid modified straw biochar, and the mass ratio of the biochar to the basalt macadam is 2.95%.
Example 18
On the basis of example 14, yellow flag is introduced, the height of the yellow flag is 300mm, and 4 plants are planted.
Example 19
On the basis of example 15, yellow flag is introduced, the height of the yellow flag is 300mm, and 4 plants are planted.
Example 20
On the basis of example 16, yellow flag is introduced, the height of the yellow flag is 300mm, and 4 plants are planted.
Example 21
On the basis of example 17, yellow flag is introduced, the height of the yellow flag is 300mm, and 4 plants are planted.
Data test two
The system of examples 6, 12, 14-21 was used to treat the same batch of municipal tail water with a COD concentration of 50mg/L and NH4 +A concentration of-N ofThe concentration of 5.0mg/L and TN is 15.0mg/L, the concentration of TP is about 1.0mg/L, the test process of the data is the same as the data test I, and comparative analysis is carried out on the purification of the urban tail water of the artificial wetland substrate of the examples 6 and 14 to 17 and the examples 12 and 18 to 21.
The results are shown in FIGS. 10-15.
FIG. 10 shows: shows that the modified biochar is used as the substrate of the artificial wetland to obviously improve the NH of the artificial wetland4 +-removal capacity of N. The concentration of ammonia nitrogen is reduced after freeze-thaw cycle modification, and the removal rate is improved. The straw biochar after freeze-thaw cycle modification treatment is subjected to acid modification treatment, so that the removal rate of ammonia nitrogen in the urban tail water is further improved. The freeze-thaw action is beneficial to improving the removal of inorganic nitrogen in soil by the biochar, the specific surface area and the total pore volume are both improved after the straw biochar is modified by sulfuric acid, and the adsorption capacity is obviously enhanced. Therefore, the effect of the freeze-thaw cycle modification and the sulfuric acid composite modification on the removal of ammonia nitrogen is integrally higher than that of the pure freeze-thaw cycle modification.
FIG. 11 shows: the removal rate of TN in each example is 75-90% on the whole, and the adsorption and ion exchange capacities of the matrix are limited, so that the removal rate of TN begins to decrease for each experimental group after the constructed wetland is operated for a period of time. The modified straw biochar has higher TN removal rate. After the biological carbon is modified, the removal capability of the constructed wetland on TN is obviously improved. The comparison shows that the potassium permanganate modified biochar has higher removal rate of ammonia nitrogen, and NO is treated by the potassium permanganate modified biochar in a coordination exchange mode3 -the-N also has higher removal rate, and further the removal rate of TN is higher.
FIG. 12 shows: the modification of the biochar alkali increases C-O functional groups, thereby improving the content of NH4 +-adsorption of N. In addition, the pH value of the NaOH modified straw biochar is higher than that of other experimental groups, and the complexing effect of functional groups such as hydroxyl (-OH), carboxyl (-COOH) and carbon-oxygen single bond (C-O) is enhanced, so that the removal of ammonia nitrogen by the alkali modified biochar is improved. Overall, each experimental group NH4 +The N removal rate is on the increasing trend; the function of the plants improves the NH pair of the artificial wetland4 +-removal of N, eachExample NH4 +The removal rate of-N continues to increase. After the biochar is modified, the adsorption capacity is enhanced. Shows that the promotion effect of the artificial wet ground on the plants is enhanced, thereby reducing the NH of the ground among experimental groups4 +-the differential effect of N.
FIG. 13 shows: the initial concentration BK value of TN in the municipal tail water is between 14.0 and 16.0 mg/L. After being purified by each artificial wetland example, the concentration is basically below 6.0 mg/L. The alkali treatment of the biochar can obviously improve the denitrification rate. The removal rate of nitrate nitrogen is obviously improved, and the removal rate of TN is further improved. In addition, higher NH of the examples4 +the-N removal rate is also an important factor for the high TN removal rate.
FIG. 14 shows: the urban tail water purified by the artificial wetland is below 3.0mg/L in each embodiment. NO of each experimental group3 -The overall N concentration tends to increase, and the removal rate tends to decrease. Shows that the modified charcoal can improve NO3 --removal capacity of N.
FIG. 15 shows: although plant introduction does not improve TN removal, it is of great significance for the sustained and stable removal of TN. The reason that the TN concentration is higher under the condition of plants is mainly that the adsorption capacity of the artificial wet substrate to nitrogen is larger during the period without plants in the early stage, so that the substrate is basically in a saturated state, and the continuous denitrification capability of the substrate is weakened. Under the condition of plants, the constructed wetland substrate needs a recovery period.
TABLE 3 first order reaction kinetics equation Linear simulation results
TABLE 4 Linear simulation results of first order reaction kinetics equations
It should be noted that:
the preparation process of the sodium hydroxide modified straw biochar comprises the following steps: 2g of straw biochar is placed into a 50mL conical flask, and then 50mL of sodium hydroxide solution with the concentration of 0.1mol/L is added. Uniformly mixing the straw biochar with alkali liquor, stirring for 1 time at an interval of 2h, soaking for 24h, filtering, washing with deionized water until the filtrate is neutral, and drying at 100 ℃ to constant weight to obtain the sodium hydroxide modified straw biochar.
The preparation process of the potassium permanganate modified straw biochar comprises the following steps: 2g of straw biochar is placed into a 50mL conical flask, and then potassium permanganate solution is added to the conical flask in an amount of 50mL, wherein the concentration of the potassium permanganate solution is 0.1 mol/L. The biochar and the potassium permanganate solution are uniformly mixed and stirred for 1 time at intervals of 2 hours. And soaking the straw biochar for 24 hours, filtering, washing with deionized water, soaking for 24 hours, washing again, and drying at 100 ℃ to constant weight to obtain the sodium hydroxide modified straw biochar.
The preparation process of the freeze-thaw cycle modified straw biochar comprises the following steps: 2g of straw biochar is taken out of water and is placed into a low-temperature refrigerator (model: DW-60W28, Zhejiang Jieshi Low-temperature Equipment Co., Ltd.) after 2g of straw biochar is placed into water and is soaked for 24 hours to reach a saturated state. The freezing time is 18 hours and the thawing time is 6 hours every day, the freezing temperature is minus 60 +/-5 ℃, and the thawing temperature is 40 +/-5 ℃. After freezing every day, washing with tap water for 3 times, wherein each day is a freeze-thaw cycle. And (3) modifying the straw biochar after 8 times of freeze-thaw cycle modification, cleaning again, and drying at 100 ℃ to constant weight to obtain the freeze-thaw cycle modified straw biochar.
The preparation process of the freeze-thaw cycle and the sulfuric acid modified straw biochar comprises the following steps: and (3) carrying out sulfuric acid modification treatment on the prepared freeze-thaw cycle modified straw biochar. Specifically, 2g of freeze-thaw cycle modified straw biochar is added into 50mL of modifier H2SO4In the solution, the concentration is 0.75mol/L, the soaking time in the modifier is 24 hours, after the soaking is finished, the solution is cleaned to be neutral and colorless, then the solution is soaked for 24 hours, and finally the solution is dried to constant weight, thus obtaining the freeze-thaw cycle and sulfurAcid modified straw biochar.
As shown in fig. 16: in the presence of plants, NH4 +-N and NO3 -Removal of N, in addition to the adsorption and ion exchange effects of the matrix, the uptake by the plants and the nitrification and denitrification of the rhizosphere microorganisms of the plants. Particularly, after the biochar is modified, ammonia nitrogen and nitrate nitrogen adsorbed on the surface and in pores of the biochar are increased, and removal of nitrification and denitrification is facilitated. In addition, the modified biochar has increased pore volume, improves living environment for more microorganisms, and can promote the growth and reproduction of the microorganisms. More inorganic Nitrogen (NH) is adsorbed on the surface and in the pores of the biochar4 +-N and NO3 --N), inorganic nitrogen is used as plant nutrient substance, and plant growth is promoted after the inorganic nitrogen is absorbed by plants. And the plants absorb more inorganic nitrogen in the growth process, so that the inorganic nitrogen adsorption amount of the biochar is reduced, and the biochar is promoted to continuously adsorb the inorganic nitrogen. Thus, there is an interactive and synergistic relationship between the substrate and the plant for the removal of inorganic nitrogen. The addition of the biochar provides enough electron co-body for denitrification reaction and promotes the denitrification reaction.
The embodiments in the present description are described in a progressive manner, each embodiment focuses on differences from other embodiments, and the same and similar parts among the embodiments are referred to each other. The device disclosed by the embodiment corresponds to the method disclosed by the embodiment, so that the description is simple, and the relevant points can be referred to the method part for description.
The previous description of the disclosed embodiments is provided to enable any person skilled in the art to make or use the present invention. Various modifications to these embodiments will be readily apparent to those skilled in the art, and the generic principles defined herein may be applied to other embodiments without departing from the spirit or scope of the invention. Thus, the present invention is not intended to be limited to the embodiments shown herein but is to be accorded the widest scope consistent with the principles and novel features disclosed herein.
Claims (10)
1. The utility model provides a vertical flow constructed wetland city tail water clean system which characterized in that includes: the water body purification substrate and the coarse sand are sequentially covered on the upper surface of the crushed stone;
wherein the water body purification substrate is a mixture of biochar and basalt macadam;
the mass ratio of the biochar to the basalt broken stone is (2.21-3.79): 100.
2. the urban tail water purification system of the vertical-flow artificial wetland according to claim 1, wherein the biochar is unmodified straw biochar with a particle size of 2-8 mm.
3. The urban tail water purification system of the vertical flow artificial wetland according to claim 1, wherein the biochar is modified straw biochar with a particle size of 2-8 mm.
Wherein the modified straw biochar is selected from potassium permanganate straw biochar, sodium hydroxide modified biochar or composite modified biochar of potassium permanganate and sodium hydroxide.
4. The urban tail water purification system of the vertical-flow constructed wetlands as claimed in claim 1, wherein the particle size of the crushed stones is 10-20 mm.
5. The urban tail water purification system of the vertical flow artificial wetland according to any one of claims 1 to 4, wherein the basalt broken stone is slightly weathered basalt broken stone, and the grain size is 2-10 mm.
6. The system for purifying the urban tail water of the vertical flow artificial wetland according to claim 5, wherein the grit is 0.5-2mm in particle size.
7. The system for purifying urban tail water of the vertical-flow artificial wetland according to claim 6, further comprising: ecosystem ofComprises little acorus calamus, the plant height of the acorus calamus is 320mm in 300-2。
8. The system for purifying the urban tail water of the vertical-flow artificial wetland according to claim 2, wherein the removal rate of TN (total twisted nematic) by the system for purifying the urban tail water of the vertical-flow artificial wetland>NH4 +-N and COD, and TN had an average removal rate of 91.91% and NH4 +The average removal rate of-N was 88.14%, and the average removal rate of COD was 73.04%.
9. The system of claim 7, wherein the average removal rate of TN is 89.92%, and NH in the system is4 +Average removal of-N86.58%, average removal of COD 88.39%, and average removal of NO3 -The average removal of-N was 91.24%.
10. The system of claim 7, wherein the modified straw biochar is selected from sodium hydroxide modified biochar, so that the average TN removal rate of the system is 88.60%, and NH content in the system is higher than that in the system4 +Average removal of-N95.21%, NO3-The average removal of-N was 89.10%.
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Citations (4)
| Publication number | Priority date | Publication date | Assignee | Title |
|---|---|---|---|---|
| CN100497197C (en) * | 2007-01-19 | 2009-06-10 | 天津市水利科学研究所 | Multiple-component filler matrix undercurrent wet land purifying and processing apparatus and undercurrent wet land purifying method |
| CN206204730U (en) * | 2016-11-24 | 2017-05-31 | 天津城建大学 | One kind is used for sponge urban road drainage system |
| CN109534623A (en) * | 2019-01-16 | 2019-03-29 | 商洛学院 | The system for improving drowned flow artificial wet land wastewater treatment efficiency is added based on charcoal |
| CN112047477A (en) * | 2020-07-10 | 2020-12-08 | 东北师范大学 | Composite flow constructed wetland domestic sewage purification system |
-
2021
- 2021-12-21 CN CN202111573311.3A patent/CN114262059A/en active Pending
Patent Citations (4)
| Publication number | Priority date | Publication date | Assignee | Title |
|---|---|---|---|---|
| CN100497197C (en) * | 2007-01-19 | 2009-06-10 | 天津市水利科学研究所 | Multiple-component filler matrix undercurrent wet land purifying and processing apparatus and undercurrent wet land purifying method |
| CN206204730U (en) * | 2016-11-24 | 2017-05-31 | 天津城建大学 | One kind is used for sponge urban road drainage system |
| CN109534623A (en) * | 2019-01-16 | 2019-03-29 | 商洛学院 | The system for improving drowned flow artificial wet land wastewater treatment efficiency is added based on charcoal |
| CN112047477A (en) * | 2020-07-10 | 2020-12-08 | 东北师范大学 | Composite flow constructed wetland domestic sewage purification system |
Cited By (1)
| Publication number | Priority date | Publication date | Assignee | Title |
|---|---|---|---|---|
| CN117263392A (en) * | 2023-11-16 | 2023-12-22 | 哈尔滨师范大学 | Anti-blocking constructed wetland structure and detection method |
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