WO2020253797A1 - 一种河湖淤泥就地处理的一体化滨岸带系统及其应用 - Google Patents

一种河湖淤泥就地处理的一体化滨岸带系统及其应用 Download PDF

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WO2020253797A1
WO2020253797A1 PCT/CN2020/096913 CN2020096913W WO2020253797A1 WO 2020253797 A1 WO2020253797 A1 WO 2020253797A1 CN 2020096913 W CN2020096913 W CN 2020096913W WO 2020253797 A1 WO2020253797 A1 WO 2020253797A1
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Prior art keywords
sludge
pipe
treatment system
silt
water
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PCT/CN2020/096913
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English (en)
French (fr)
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李祎飞
邹华
廉杰
丁剑楠
付善飞
王震宇
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江南大学
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Publication of WO2020253797A1 publication Critical patent/WO2020253797A1/zh
Priority to US17/527,257 priority Critical patent/US20220073392A1/en

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    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F3/00—Biological treatment of water, waste water, or sewage
    • C02F3/32—Biological treatment of water, waste water, or sewage characterised by the animals or plants used, e.g. algae
    • C02F3/327—Biological treatment of water, waste water, or sewage characterised by the animals or plants used, e.g. algae characterised by animals and plants
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F11/00—Treatment of sludge; Devices therefor
    • C02F11/02—Biological treatment
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F3/00—Biological treatment of water, waste water, or sewage
    • C02F3/32—Biological treatment of water, waste water, or sewage characterised by the animals or plants used, e.g. algae
    • E—FIXED CONSTRUCTIONS
    • E02—HYDRAULIC ENGINEERING; FOUNDATIONS; SOIL SHIFTING
    • E02B—HYDRAULIC ENGINEERING
    • E02B3/00—Engineering works in connection with control or use of streams, rivers, coasts, or other marine sites; Sealings or joints for engineering works in general
    • E02B3/04—Structures or apparatus for, or methods of, protecting banks, coasts, or harbours
    • E02B3/12—Revetment of banks, dams, watercourses, or the like, e.g. the sea-floor
    • E—FIXED CONSTRUCTIONS
    • E02—HYDRAULIC ENGINEERING; FOUNDATIONS; SOIL SHIFTING
    • E02D—FOUNDATIONS; EXCAVATIONS; EMBANKMENTS; UNDERGROUND OR UNDERWATER STRUCTURES
    • E02D31/00—Protective arrangements for foundations or foundation structures; Ground foundation measures for protecting the soil or the subsoil water, e.g. preventing or counteracting oil pollution
    • E02D31/002—Ground foundation measures for protecting the soil or subsoil water, e.g. preventing or counteracting oil pollution
    • E02D31/006—Sealing of existing landfills, e.g. using mining techniques
    • E—FIXED CONSTRUCTIONS
    • E03—WATER SUPPLY; SEWERAGE
    • E03F—SEWERS; CESSPOOLS
    • E03F3/00—Sewer pipe-line systems
    • E03F3/02—Arrangement of sewer pipe-lines or pipe-line systems
    • E—FIXED CONSTRUCTIONS
    • E03—WATER SUPPLY; SEWERAGE
    • E03F—SEWERS; CESSPOOLS
    • E03F5/00—Sewerage structures
    • E03F5/20—Siphon pipes or inverted siphons
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F2101/00—Nature of the contaminant
    • C02F2101/10—Inorganic compounds
    • C02F2101/105—Phosphorus compounds
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F2101/00—Nature of the contaminant
    • C02F2101/10—Inorganic compounds
    • C02F2101/16—Nitrogen compounds, e.g. ammonia
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F2103/00—Nature of the water, waste water, sewage or sludge to be treated
    • C02F2103/007—Contaminated open waterways, rivers, lakes or ponds
    • Y—GENERAL TAGGING OF NEW TECHNOLOGICAL DEVELOPMENTS; GENERAL TAGGING OF CROSS-SECTIONAL TECHNOLOGIES SPANNING OVER SEVERAL SECTIONS OF THE IPC; TECHNICAL SUBJECTS COVERED BY FORMER USPC CROSS-REFERENCE ART COLLECTIONS [XRACs] AND DIGESTS
    • Y02—TECHNOLOGIES OR APPLICATIONS FOR MITIGATION OR ADAPTATION AGAINST CLIMATE CHANGE
    • Y02W—CLIMATE CHANGE MITIGATION TECHNOLOGIES RELATED TO WASTEWATER TREATMENT OR WASTE MANAGEMENT
    • Y02W10/00—Technologies for wastewater treatment
    • Y02W10/10—Biological treatment of water, waste water, or sewage

Definitions

  • the invention relates to an integrated coastal zone system for on-site treatment of river and lake silt and its application, and belongs to the technical field of river and lake silt treatment.
  • Silt is a kind of sediment that gradually settles to the bottom layer of the water body through various physical, chemical and biological actions in a static or slow flowing water environment.
  • the silt has a high natural moisture content, strong compressibility, and is often gray-black, rich in organic matter, minerals and heavy metals.
  • Nutrients such as nitrogen and phosphorus accumulated in the silt at the bottom of rivers and lakes can be directly ingested by microorganisms on the one hand, enter the food chain, and participate in the cycle of aquatic ecosystems; on the other hand, under certain environmental conditions, they can be released from the bottom silt Re-enter the water body, thus forming the internal pollution of rivers and lakes.
  • domestic and foreign sludge treatment technologies mainly include: traditional yard method, underwater throwing sludge method, vacuum preloading method, physical dehydration consolidation method, high temperature melting sintering method and chemical solidification method.
  • the traditional yard method has large processing capacity, simple construction technology and equipment, and low cost, but it covers a large area, is difficult to acquire land, and is prone to secondary pollution; the underwater dumping method dumps silt into the sea, which will cause damage to the marine environment.
  • the construction machinery and equipment of the vacuum preloading method are simple and easy to operate, but its shortcomings are also very obvious, requiring a large number of storage yards , It takes a long time and is easy to cause secondary pollution;
  • the physical dehydration consolidation method is only suitable for small batches of sludge treatment, which has high energy consumption and high cost;
  • the high-temperature melting sintering method can burn sludge into building materials, but its sludge treatment capacity Low, high energy consumption, high cost; although the chemical solidification method has relatively mature process equipment and can be processed in large quantities, it still requires a large number of storage yards, and the high moisture content of the sludge makes the treatment costly.
  • Phytoremediation technologies (such as constructed wetlands, ecological filter beds) have the advantages of low investment, simple management, and low operating costs, and are low-carbon, environmentally friendly ecological technologies.
  • Phytoremediation technology is widely used to treat sewage and is promoted in the field of improving the water quality of rivers and lakes.
  • the application of phytoremediation technology to treat silt is very rare.
  • the current patents related to silt phytoremediation technology include: 1) A method of wetland silt treatment (application number 201710068301.1), which digs and builds a backfill pond, and uses rice seedling throwing technology to throw wet plants in the backfill pond.
  • the silt treatment is achieved by building a plant community, but the water in the draining area of the backfill pond is directly discharged, which is easy to cause secondary pollution to the environment; 2)
  • the silt purification and adjustment system (application number 201610479546.9), which uses the silt landfill pond purification and adjustment
  • the sludge can eliminate the odor-prone defects in the sludge landfill, but the sludge leachate collected by the overflow well is not considered for advanced treatment, which is not conducive to direct discharge or reuse;
  • the floating greening treatment process structure (application number 201710186061.5) provides a method for planting plants in the sludge (or sludge) pond formed by the landfill of urban sludge (or sludge), which can achieve dewatering and dewatering of sludge to a certain extent.
  • the present invention is based on phytoremediation technology and constructs an integrated coastal zone system for treating river and lake silt on site.
  • the invention can flexibly carry out engineering construction according to the topography of rivers and lakes. Through the transpiration and absorption of plants, the filtration and adsorption of fillers, and the degradation of microorganisms, the dehydration and harmlessness of silt and the sludge infiltration can be effectively realized. Advanced treatment of filtrate and purification of part of river/lake water.
  • the entire integrated coastal zone system realizes the on-site treatment of river and lake sludge.
  • the construction investment cost is low, the management and operation are simple and the cost is low, it is environmentally friendly and is not easy to cause secondary pollution.
  • the dried sludge can be used as organic fertilizer. Used in green land or farmland, the effluent after leachate treatment can be directly discharged into rivers or lakes.
  • the first object of the present invention is to provide an integrated coastal zone system for on-site treatment of river and lake sludge, including three subsystems: silt ecological treatment, siphon drainage, and sludge leachate advanced treatment;
  • the sludge ecological treatment system is from the top Plants, fillers, aeration pipes and water collection pipes are arranged below, and the vent pipes are connected to the water collection pipe;
  • the siphon pipe in the siphon drainage system is of retractable hump type;
  • the advanced treatment of sludge leachate includes the first-stage ecological treatment unit upflow Type wetland and second-level ecological treatment unit surface flow wetland.
  • the filler of the silt ecological treatment system is arranged in layers from bottom to top, including a drainage layer (10-30cm in thickness, gravel with a diameter of 10-30mm) and a transition layer (5-20cm in thickness, diameter 4-15mm gravel), filter layer (15-45cm thick, 0.5-5mm diameter gravel/zeolite/sand/ceramsite/volcanic stone), cover layer (5-15cm thick, 8-20mm diameter gravel), each Lay a geotextile with good water permeability between the layers to prevent the filling of each layer from mixing during aeration.
  • the bottom slope of the silt ecological treatment system is 0.1%-0.3%, and a perforated water collection pipe is provided, and the water collection pipe is connected to the vent pipe.
  • the inner diameter of the pipe is 8-15 cm, and the vent pipe is 15-cm higher than the tank body. 30cm;
  • the aeration pipe is adjacent to and set on the water collection pipe, and the water collection pipe and the vent pipe are respectively wrapped with geotextile.
  • the pool body of the siphon drainage system is prefabricated with reinforced concrete
  • the shape of the siphon is a hump
  • the horizontal inclination of the rising section is 30-45°
  • a vacuum breaking valve is set on the top of the hump
  • the siphon is designed to be telescopic
  • the height of the siphon can be flexibly adjusted to 15-50cm
  • the apex of the hump is 15-35cm higher than the collection pipe of the silt ecological treatment system
  • the water level of the siphon is 20-40cm lower than the water level of the collection pipe
  • the inner diameter of the siphon is 8-15cm.
  • the filler of the upflow wetland of the first-stage ecological treatment unit of the sludge leachate advanced treatment system is arranged in layers from bottom to top, including the water inlet layer (thickness 10-30cm, diameter 10- 30mm gravel), filter layer (15-30cm thickness, 0.5-5mm diameter gravel/zeolite/sand/ceramsite/volcanic stone) and drainage layer (thickness 10-30cm, diameter 10-30mm gravel).
  • the perforated water inlet pipe and the drain pipe of the upflow wetland are respectively arranged in the water inlet layer and the drainage layer.
  • the inner diameter of the pipe is 8-15cm, and the water level difference between the two pipes is 20-40cm.
  • the water level of the water pipe is 40-60cm below the apex of the siphon hump.
  • the water level of the surface flow wetland of the second-level ecological treatment unit of the sludge leachate advanced treatment system is the same as that of the river/lake, separated by wooden piles, and the treated effluent can be directly discharged into the river and lake. , When the wetland water is insufficient, the river/lake water will automatically be added to the surface flow wetland.
  • the bottom and wall of the sludge ecological treatment system and the sludge leachate advanced treatment system are laid with PE anti-seepage membranes, and geotextiles are laid between each layer of filler.
  • the second object of the present invention is to apply the above-mentioned integrated coastal zone system for silt treatment method, and the method is:
  • a perforated water collection pipe is laid at the bottom of the sludge ecological treatment system, and the collected leachate enters the sludge leachate advanced treatment system through the siphon drainage system.
  • the siphon drainage system can automatically control the water level and realize intermittent drainage;
  • the silt in the step (1) is silt with a water content of more than 70% in rivers and lakes, and is added at a load of 50-80 kg dry matter/(m 2 ⁇ a), and layered Spread it flat on the covering layer of the silt ecological treatment system, and do it every 30-60 days, and the thickness of each dosing does not exceed 15cm. Until the tank is filled, the final height of the filling is 0.5-1.2m. The water content drops below 50% for removal.
  • the aeration interval period is 15-30 days, the aeration volume is 50-100 mL/min, and the aeration time is 1-2 days.
  • emergent plants are planted in the silt ecological treatment system, emergent plants and phytophytes are planted in the upflow wetland of the sludge leachate advanced treatment system, and emergent plants and floating leaf plants are planted in the surface stream wetland. And submerged plants.
  • the third object of the present invention is to provide an application of an integrated coastal zone system in the field of silt treatment.
  • the integrated coastal zone system of the present invention can flexibly carry out engineering construction according to the topography of rivers and lakes, and realize the on-site treatment of silt. There is no need to transport the silt out and then conduct centralized treatment, and the construction investment cost is low;
  • the sludge ecological treatment system in the integrated coastal zone system can effectively achieve the dehydration and harmlessness of the sludge, and the treated sludge can be reused as organic fertilizer in the surrounding green land or farmland to realize the resource utilization of the sludge;
  • the invention utilizes the synergy between the sludge ecological treatment system and the sludge leachate advanced treatment system.
  • the water content of the sludge is reduced from 90% to 45%, and the COD, TN, TP, ammonia nitrogen, copper, mercury, and arsenic of the effluent Concentrations of other pollutants are low, reaching Class III water quality standards, and can be directly discharged into rivers/lakes, and the removal rate of each pollutant is above 70%;
  • the management and operation of the integrated coastal zone system are simple. In addition to the aeration cost of the sludge ecological treatment system, the siphon drainage system and the sludge leachate advanced treatment system do not require power, no power costs, and the overall system management and operation costs are low ;
  • Planting a variety of wetland plants in the integrated coastal zone system can create a good landscape effect and beautify the coastal environment of rivers or lakes.
  • Figure 1 is a schematic diagram of an integrated coastal zone system for in-situ treatment of river silt.
  • FIG. 2 is a schematic diagram of the river silt ecological treatment system.
  • Figure 3 is a schematic diagram of a river siphon drainage system.
  • Figure 4 is a schematic diagram of an advanced treatment system for river sludge leachate.
  • Figure 5 is a schematic diagram of the silt landfill pond on the river bank.
  • silt ecological treatment system 1. silt ecological treatment system, 2. siphon drainage system, 3. sludge leachate advanced treatment system-upflow wetland, 4. sludge leachate advanced treatment system-surface flow wetland, 5. river course, 6. silt ecology Treatment system drainage layer, 7. silt ecological treatment system transition layer, 8. silt ecological treatment system filter layer, 9. silt ecological treatment system cover layer, 10. silt ecological treatment system silt layer, 11. silt ecological treatment system aeration pipe , 12. Silt ecological treatment system vent pipe, 13. Silt ecological treatment system collection pipe, 14. Siphon pipe, 15. Upflow wetland inlet layer, 16. Upflow wetland filter layer, 17. Upflow wetland drainage layer , 18. Drainage layer of silt landfill pond, 19. Collection well of silt landfill pond.
  • the present invention provides a low-cost and environmentally friendly integrated coastal zone system for on-site treatment of river and lake sludge.
  • the present invention will be further described in detail below with reference to the accompanying drawings.
  • Detection method of sludge moisture content According to GBT 24602-2009 "Urban Sewage Treatment Sludge Disposal Separate Incineration Mud Quality", the recommended standard method for the determination of sludge moisture content determination is CJ/T221-2005 "Urban Sewage Treatment Plant Sludge Inspection Method” ⁇ The gravimetric method for determination.
  • COD detection method refer to the national standard GB11914-89 potassium dichromate method for determination.
  • TN detection method refer to the national standard GB11894-89 alkaline potassium persulfate digestion ultraviolet spectrophotometry for determination.
  • TP detection method refer to the national standard GB11893-89 ammonium molybdate spectrophotometric method for determination.
  • Ammonia nitrogen detection method refer to the national standard 7479-87 Nessler's reagent spectrophotometric method for determination.
  • Heavy metal copper detection method refer to the national standard GB/T7475-1987 atomic absorption spectrophotometry for determination.
  • Heavy metal mercury detection method refer to the national standard GB/T7468-1987 atomic absorption spectrophotometry for determination.
  • Heavy metal arsenic detection method refer to the national standard GB/T7485-1987 silver diethyldithiocarbamate spectrophotometric method for determination.
  • an integrated coastal zone system for on-site treatment of silt according to the present invention (as shown in Figure 1) is set up.
  • the system is 20m long and 16m wide.
  • the silt dredged from the river course is first spread in the silt ecological treatment system.
  • the collected leachate enters the sludge leachate advanced treatment system through the siphon drainage system for treatment, and the effluent is finally discharged into the river course.
  • the silt ecological treatment system is shown in Figure 2.
  • the cross-section of the system is trapezoidal, with the bottom bottom being 2m long and the top bottom being 4.6m long.
  • the final height of the silt can reach 0.8m.
  • the filler is arranged in layers from bottom to top, including drainage layer (15cm thick, 10-30mm diameter gravel), transition layer (10cm thick, 4-15mm diameter gravel), filter layer (thickness 25cm, 0.5-5mm diameter volcano Stone), covering layer (10cm in thickness, 8-20mm diameter gravel), and geotextile is laid between each layer.
  • the bottom slope is 0.2%, and a perforated water collection pipe is set, which is connected to the vent pipe.
  • the inner diameter of the pipe is 8cm.
  • the vent pipe is 15cm higher than the tank body.
  • the water collection pipe and the vent pipe are respectively wrapped with geotextile.
  • the aeration tube is set above the water collection tube, the aeration interval is 15 days, the aeration volume is 80 mL/min, and the aeration time is 2 days.
  • the bottom and wall of the pool adopt PE impermeable membrane, and the plants are mixed with reeds, cattails and calamus, and the planting density is 15 plants/m 2 .
  • the siphon drainage system is shown in Figure 3.
  • the siphon is telescopic and has a hump shape.
  • the horizontal inclination of the hump rise section is 45°, and a vacuum breaking valve is designed at the top of the hump.
  • the apex of the siphon is 15cm higher than the collection pipe of the silt ecological treatment system, and the stretchable height of the siphon is 20cm.
  • the outlet water level of the siphon is 30cm lower than the water level of the collection pipe, and the inner diameter of the siphon is 8cm.
  • the sludge leachate advanced treatment system is shown in Figure 4.
  • the bottom and wall of the two-stage ecological treatment unit are all made of PE anti-seepage membrane.
  • the filler of the upflow wetland is arranged in layers from bottom to top, including the water inlet layer (15cm thick, 10-30mm diameter gravel), filter layer (thickness 20cm, 0.5-5mm diameter volcanic rock), and drainage layer (thickness 15cm, 10-30mm diameter gravel).
  • the perforated water inlet pipe and the drain pipe of the upflow wetland are respectively arranged in the water inlet and drainage layers, with an inner diameter of 8cm, and the water level difference between the two pipes is 28cm.
  • the water level of the water inlet pipe is 60cm lower than the apex of the siphon.
  • the water level of the surface flow wetland is the same as that of the river/lake, separated by wooden piles.
  • Up-flow and surface-flow wetlands are mixed with a variety of aquatic plants such as reeds, calamus, canna, rushes, etc., and floating-leaf plants such as water lilies are dotted with water lilies to create a landscape.
  • the moisture content of the sludge has been reduced from 90% to 45%.
  • the effluent will be polluted by COD, TN, TP, ammonia nitrogen, copper, mercury, arsenic, etc.
  • the removal rate of substances reached 75% or more, and the concentrations were 14.5mg/L, 0.5mg/L, 0.13mg/L, 0.4mg/L, 0.9mg/L, 0.0008mg/L, 0.045mg/L, reaching three Similar to water quality standards, it can be directly discharged into the river.
  • the moisture content of the untreated sludge is 90%.
  • the concentration of COD, TN, TP, ammonia nitrogen, copper, mercury, arsenic and other pollutants in the leachate is shown in Table 1. It belongs to the inferior category five water and cannot be directly discharged into the river. .
  • Example 1 Using only the sludge ecological treatment system in Example 1 (without advanced leachate treatment), the water content of the sludge after treatment was 47%, and the COD, TN, TP, ammonia nitrogen, copper, mercury, arsenic and other pollutants in the effluent The concentration is shown in Table 1. It belongs to five types of water and cannot be directly discharged into the river.
  • the sludge landfill pond and leachate advanced treatment system of Comparative Example 2 are used, and the remaining operation steps are the same as those of Example 1.
  • the water content of the sludge after treatment is 79%, and the COD, TN, TP, ammonia nitrogen, copper, mercury,
  • the concentration of arsenic and other pollutants is shown in Table 1, which belongs to the inferior category five water and cannot be directly discharged into the river.
  • the water content of the sludge after treatment is 52%, and the concentration of COD, TN, TP, ammonia nitrogen, copper, mercury, arsenic and other pollutants in the effluent is shown in the table 1. It belongs to the five types of water and cannot be directly discharged into the river.
  • Example 1 The data of Example 1 and Comparative Examples 2-4 in Table 1 are converted to obtain the pollutant removal effect of separate treatment of different units, as shown in Table 2.
  • Example 1 of the present invention the contents of pollutants COD, TN, ammonia nitrogen and arsenic in the effluent treated by the sludge ecological treatment system and the leachate advanced treatment system are 14.5 mg/L, 0.5 mg/L, 0.4 mg/L and 0.045, respectively mg/L, compared to Comparative Example 2, the removal rates of pollutants COD, TN, ammonia nitrogen and arsenic reached 69.98%, 88.37%, 88.89% and 67.86%, respectively, which is better than the sludge ecological treatment system alone and the leachate depth alone
  • the sum of the effects of the treatment system (61.70%, 72.09%, 86.11% and 54.29%, respectively) is superior, indicating that the addition of sludge ecological treatment system and
  • the horizontal angle is set to 45° in consideration of the problem of land occupation.
  • the water filling flow rate of the siphon in Example 1 was 0.0025m 3 /s.
  • Comparative Example 6 the hump-shaped siphon tube in the siphon drainage system was replaced with a U-shape, and the water filling flow rate of the siphon was 0.0020m 3 /s.
  • the water filling flow rate of the siphon of Example 1 is greater than that of Comparative Example 6, indicating that the siphon effect of the hump-type siphon is better.

Abstract

本发明公开了一种河湖淤泥就地处理的一体化滨岸带系统及其应用，属于淤泥处理技术领域。该一体化系统由淤泥生态处理、虹吸排水和淤泥渗滤液深度处理三个子系统组成；淤泥生态处理系统自上而下设置植物、填料、曝气管和集水管，通气管与集水管相连；虹吸排水系统中的虹吸管为可伸缩式驼峰型；淤泥渗滤液深度处理包括第一级生态处理单元升流式湿地和第二级生态处理单元表面流湿地。本发明通过植物的蒸腾和吸收作用、填料的过滤和吸附作用及微生物的降解作用，有效实现淤泥的脱水和无害化、淤泥渗滤液的深度处理以及部分河/湖水的净化。

Description

一种河湖淤泥就地处理的一体化滨岸带系统及其应用 技术领域
本发明涉及一种河湖淤泥就地处理的一体化滨岸带系统及其应用，属于河湖淤泥处理技术领域。
背景技术
淤泥是一种在静水或缓慢的流水环境中经各种物理、化学和生物作用，逐渐沉降至水体底质表层的沉积物。淤泥天然含水率很高，压缩性强，常呈灰黑色，富含有机物、矿物质及重金属等物质。积累在河道和湖泊底部淤泥的氮、磷等营养物质，一方面可以被微生物直接摄入，进入食物链，参与水生生态系统的循环；另一方面在一定环境条件下，可以从底泥中释放出来重新进入水体，从而形成河湖的内源污染。河湖的淤泥过多往往会引起水体富营养化、水质黑臭、水生生物数量大规模减少等问题。针对这些问题，清淤是河湖治理中一个必不可少的环节，可以有效地控制内源污染。然而，由于淤泥的特性，从河湖清理出来的淤泥如何进行处理是一大难题。
目前，国内外处理淤泥的技术主要有：传统堆场法、水下抛泥法、真空预压法、物理脱水固结法、高温熔融烧结法和化学固化法等。传统堆场法的处理量大、施工工艺设备简单、造价较低，但其占地面积大、征地困难、很容易形成二次污染；水下抛泥法是将淤泥倾倒入海，会给海洋环境带来不良影响，随着海洋保护力度的加大，该方法的使用逐渐受到各方面的限制；真空预压法的施工机具和设备简单、易于操作，但其缺点也非常明显，需要大量堆场、占用时间长、易造成二次污染；物理脱水固结法只适用于小批量的淤泥处理，能耗大且成本高；高温熔融烧结法可将淤泥烧制成建筑材料，但其淤泥处理量低、能耗大、成本高；化学固化法虽然有比较成熟的工艺设备，可大批量处理，但是仍然需要大量堆场，并且淤泥的高含水率使处理代价很大。上述技术皆是将淤泥进行外运，然后进行集中处理，不仅费时费力，而且易造成二次污染。因而，寻找一种可以将淤泥就地处理、成本低、对环境友好的技术具有重要的应用意义。
植物修复技术(如人工湿地、生态滤床)具有投资少、管理简单、运行费用低等优点，属于低碳、环保型的生态技术。植物修复技术被广泛用于处理污水，并且在河道和湖泊水质提升领域得到推广，然而，采用植物修复技术处理淤泥的应用很少。经过检索，目前有关淤泥植物修复技术的专利包括：1)一种湿地淤泥治理的方法(申请号201710068301.1)，该方法挖建回填池，采用水稻抛秧技术将湿生植物抛撒种植在回填池中，以营建植物群落实现淤 泥的治理，但回填池沥水区的水直接外排，易给环境带来二次污染；2)淤泥净化调节处理系统(申请号201610479546.9)，采用淤泥填埋塘净化调节淤泥，可以消除淤泥填埋中易产生臭气的缺陷，但溢流井收集的淤泥渗滤液没有考虑进行深度处理，不利于直接外排或回用；3)一种污泥(或淤泥)塘浮式绿化处理工艺结构(申请号201710186061.5)，提供了一种城市污泥(或淤泥)填埋形成的污泥(或淤泥)塘中种植植物的方法，可以在一定程度上实现淤泥的脱水和资源化，但对淤泥的处理并不彻底，不适于就地处理的推广。因此，需要找到一种能够充分利用植物修复技术的优势，就地处理淤泥，实现淤泥的脱水和无害化，并且可以对淤泥渗滤液进行深度处理的一体化系统。
发明内容
为解决上述问题，本发明基于植物修复技术，构建了一种就地处理河湖淤泥的一体化滨岸带系统。本发明可以根据河道、湖泊岸边的地形灵活地进行工程建设，通过植物的蒸腾和吸收作用、填料的过滤和吸附作用、及微生物的降解作用，有效实现淤泥的脱水和无害化、淤泥渗滤液的深度处理、以及部分河/湖水的净化。整个一体化滨岸带系统实现了河湖淤泥的就地处理，建设投资成本低、管理和运行简单且费用少、对环境友好且不易造成二次污染、干化后的淤泥可以作为有机肥回用于绿地或农田、渗滤液处理后的出水可以直接排入河道或湖泊。
本发明的第一个目的是提供一种就地处理河湖淤泥的一体化滨岸带系统，包括淤泥生态处理、虹吸排水、淤泥渗滤液深度处理三个子系统；所述淤泥生态处理系统自上而下设置植物、填料、曝气管和集水管，通气管与集水管相连；虹吸排水系统中的虹吸管为可伸缩式驼峰型；所述淤泥渗滤液深度处理包括第一级生态处理单元升流式湿地和第二级生态处理单元表面流湿地。
在本发明的一种实施方式中，淤泥生态处理系统的填料自下而上分层设置，包括排水层(厚度10-30cm，直径10-30mm的砾石)、过渡层(厚度5-20cm，直径4-15mm的砾石)、过滤层(厚度15-45cm，直径0.5-5mm的砾石/沸石/砂/陶粒/火山石)、覆盖层(厚度5-15cm，直径8-20mm的砾石)，各层之间铺设透水性良好的土工布，防止曝气时各层填料相混合。
在本发明的一种实施方式中，淤泥生态处理系统底部坡度为0.1％-0.3％，设置穿孔集水管，集水管与通气管相连，管道内径为8-15cm，通气管高出池体15-30cm；所述曝气管紧邻集水管并设置在其之上，用土工布分别将集水管与通气管包裹。
在本发明的一种实施方式中，虹吸排水系统的池体采用钢筋混凝土预制，虹吸管形状为驼峰型，上升段水平倾角为30-45°，在驼峰顶部设置真空破坏阀，虹吸管设计成伸缩式，可 灵活调节虹吸管的高度为15-50cm，驼峰顶点高于淤泥生态处理系统集水管15-35cm，虹吸管出水水位低于集水管水位20-40cm，虹吸管内径为8-15cm。
在本发明的一种实施方式中，淤泥渗滤液深度处理系统的第一级生态处理单元升流式湿地的填料自下而上分层设置，包括进水层(厚度10-30cm，直径10-30mm的砾石，)、过滤层(厚度15-30cm，直径0.5-5mm的砾石/沸石/砂/陶粒/火山石)和排水层(厚度10-30cm，直径10-30mm的砾石)。
在本发明的一种实施方式中，升流式湿地的穿孔进水管和排水管分别设置在进水层和排水层内，管道内径为8-15cm，两管的水位差为20-40cm，进水管的水位低于虹吸管驼峰顶点40-60cm。
在本发明的一种实施方式中，淤泥渗滤液深度处理系统的第二级生态处理单元表面流湿地的水位与河道/湖泊相同，采用木桩相隔，处理后的出水可以直接外排进入河道湖泊，湿地水量不足时，河/湖水自动补充到表面流湿地中。
在本发明的一种实施方式中，淤泥生态处理系统和淤泥渗滤液深度处理系统的池底及池壁铺设PE防渗膜，各层填料之间铺设土工布。
本发明的第二个目的是应用上述一体化滨岸带系统进行淤泥处理的方法，所述方法为：
(1)淤泥生态处理：淤泥生态处理系统的覆盖层种植植物，淤泥定期排入，淤泥生态处理系统内部配置通气管和曝气管，每隔一定周期曝气一次以加快污泥处理速度、保障氧气传递、并有效避免填料的堵塞；利用植物、填料及微生物的协同作用，实现淤泥的脱水和无害化；
(2)淤泥生态处理系统底部铺设穿孔集水管，收集的渗滤液通过虹吸排水系统进入淤泥渗滤液深度处理系统，虹吸排水系统可以自动控制水位、实现间歇排水；
(3)在淤泥渗滤液深度处理系统中，渗滤液依次经过升流式和表面流湿地的两级生态处理，出水可以达标排入河道或湖泊，水量不足时河/湖水可以进入表面流湿地，实现部分河/湖水的净化。
在本发明的一种实施方式中，所述步骤(1)淤泥为河道和湖泊含水率高于70％的淤泥，以50-80kg干物质/(m 2·a)的负荷投加，分层平铺在淤泥生态处理系统的覆盖层之上，每隔30-60天投加一次，每次投加厚度不超过15cm，至池体填满为止，填充的最终高度为0.5-1.2m，含水率降至50％以下进行清除。
在本发明的一种实施方式中，曝气间隔周期为15-30天，曝气量为50-100mL/min，曝气时间为1-2天。
在本发明的一种实施方式中，淤泥生态处理系统种植挺水植物，淤泥渗滤液深度处理系统的升流式湿地种植挺水植物和湿生植物，表面流湿地种植挺水植物、浮叶植物和沉水植物。
本发明第三个目的是提供一种一体化滨岸带系统在淤泥处理领域的应用。
有益效果：
(1)本发明的一体化滨岸带系统可以根据河道、湖泊岸边的地形灵活地进行工程建设，实现淤泥的就地处理，不需要将淤泥外运再进行集中处理，建设投资成本低；
(2)一体化滨岸带系统中的淤泥生态处理系统可以有效实现淤泥的脱水和无害化，并可以将处理后的淤泥作为有机肥回用于周边绿地或农田，实现淤泥的资源化；
(3)一体化滨岸带系统中的淤泥渗滤液深度处理系统将渗滤液处理达标后外排进入河道或湖泊，对环境友好不造成二次污染，并且还实现部分河/湖水的净化，改善河/湖水质；
(4)通过植物的蒸腾和吸收作用、填料的过滤和吸附作用、及微生物的降解作用，有效实现淤泥的脱水和无害化、淤泥渗滤液的深度处理、以及部分河/湖水的净化，本发明利用淤泥生态处理系统和淤泥渗滤液深度处理系统之间的协同作用，处理后淤泥的含水量由原来的90％降至45％，出水的COD、TN、TP、氨氮、铜、汞、砷等污染物浓度低，达到三类水质标准，可直接排入河道/湖泊中，且各污染物去除率皆达到70％以上；
(5)一体化滨岸带系统的管理和运行简单，除了淤泥生态处理系统的曝气费用，虹吸排水系统和淤泥渗滤液深度处理系统无需电源，不产生动力费用，整个系统的管理运行费用低；
(6)一体化滨岸带系统种植多种湿地植物，可以营造良好的景观效果，从而美化河道或湖泊的滨岸环境。
附图说明
图1是河道淤泥就地处理的一体化滨岸带系统示意图。
图2是河道淤泥生态处理系统示意图。
图3是河道虹吸排水系统示意图。
图4是河道淤泥渗滤液深度处理系统示意图。
图5是河道岸边淤泥填埋池示意图。
其中，1.淤泥生态处理系统，2.虹吸排水系统，3.淤泥渗滤液深度处理系统-升流式湿地，4.淤泥渗滤液深度处理系统-表面流湿地，5.河道，6.淤泥生态处理系统排水层，7.淤泥生态处理系统过渡层，8.淤泥生态处理系统过滤层，9.淤泥生态处理系统覆盖层，10.淤泥生态处理系统淤泥层，11.淤泥生态处理系统曝气管，12.淤泥生态处理系统通气管，13.淤泥生态处理系统集水管，14.虹吸管，15.升流式湿地进水层，16.升流式湿地过滤层，17.升 流式湿地排水层，18.淤泥填埋池排水层，19.淤泥填埋池的集水井。
具体实施方式
本发明提供一种成本低、对环境友好的就地处理河湖淤泥的一体化滨岸带系统，下面结合附图对本发明作进一步的详细说明。
下述实施例和对比例中涉及到的检测方法如下：
1、淤泥含水率检测方法：依据GBT 24602-2009《城镇污水处理污泥处置单独焚烧用泥质》推荐检测污泥含水率测定标准方法为CJ/T221-2005《城市污水处理厂污泥检验方法》中的重量法进行测定。
2、COD检测方法：参照国标GB11914-89重铬酸钾法进行测定。
3、TN检测方法：参照国标GB11894-89碱性过硫酸钾消解紫外分光光度法进行测定。
4、TP检测方法：参照国标GB11893-89钼酸铵分光光度法进行测定。
5、氨氮检测方法：参照国标7479-87纳氏试剂分光光度法进行测定。
6、重金属铜检测方法：参照国标GB/T7475-1987原子吸收分光光度法进行测定。
7、重金属汞检测方法：参照国标GB/T7468-1987原子吸收分光光度法进行测定。
8、重金属砷检测方法：参照国标GB/T7485-1987二乙基二硫代氨基甲酸银分光光度法进行测定。
实施例1：
在无锡某条河道岸边，设置本发明就地处理淤泥的一体化滨岸带系统(如图1)，该系统长20m，宽16m。从河道清淤出来的淤泥首先平铺在淤泥生态处理系统，收集的渗滤液经过虹吸排水系统进入淤泥渗滤液深度处理系统进行处理，出水最后排入河道。
淤泥生态处理系统如图2所示，该系统的剖面为梯形，下底长2m，上底长4.6m，淤泥最终高度可达0.8m。填料自下而上分层设置，包括排水层(厚度15cm，10-30mm直径的砾石)、过渡层(厚度10cm，4-15mm直径的砾石)、过滤层(厚度25cm，0.5-5mm直径的火山石)、覆盖层(厚度10cm，8-20mm直径的砾石)，各层之间铺设土工布。底部坡度为0.2％，设置穿孔集水管，与通气管相连，管道内径为8cm，通气管高出池体15cm，用土工布分别将集水管与通气管包裹。曝气管设置在集水管之上，曝气间隔周期为15天，曝气量为80mL/min，曝气时间为2天。池底及池壁采用PE防渗膜，植物混合种植芦苇、香蒲、菖蒲，种植密度为15株/m 2。
虹吸排水系统如图3所示，虹吸管为伸缩式，形状为驼峰型，驼峰上升段的水平倾角为45°，在驼峰顶点设计真空破坏阀。虹吸管顶点高于淤泥生态处理系统集水管15cm，虹吸 管可拉伸高度为20cm。虹吸管出水水位低于集水管水位30cm，虹吸管内径为8cm。
淤泥渗滤液深度处理系统如图4所示，两级生态处理单元的池底及池壁皆采用PE防渗膜。升流式湿地的填料自下而上分层设置，包括进水层(厚度15cm，10-30mm直径的砾石)、过滤层(厚度20cm，0.5-5mm直径的火山石)、和排水层(厚度15cm，10-30mm直径的砾石)。升流式湿地的穿孔进水管和排水管分别设置在进水层和排水层内，内径为8cm，两管水位差为28cm，进水管的水位低于虹吸管顶点60cm。表面流湿地的水位与河道/湖泊相同，采用木桩相隔。升流式和表面流湿地混种芦苇、菖蒲、美人蕉、灯心草等多种水生植物，表面流湿地点缀睡莲等浮叶植物，营造景观。
该一体化系统经过6个月的运行，淤泥的含水率由原来的90％降至45％，淤泥渗滤液经深度处理后，出水的COD、TN、TP、氨氮、铜、汞、砷等污染物的去除率皆达到75％以上，浓度分别为14.5mg/L、0.5mg/L、0.13mg/L、0.4mg/L、0.9mg/L、0.0008mg/L、0.045mg/L,达到三类水质标准，可直接排入河道中。
对比例1：
未经处理的淤泥的含水率为90％，渗滤液中的COD、TN、TP、氨氮、铜、汞、砷等污染物的浓度见表1，属于劣五类水，不能直接排放到河道中。
对比例2：
在同样的河道岸边挖建一个尺寸和形状与淤泥生态处理系统相同的常规淤泥填埋池(图5，没有植物、填料、曝气管和通气管)，将淤泥平铺在淤泥填埋池中，每次填埋15cm。填埋池底部设置排水层(厚度15cm，20mm直径的砾石)，排水层中铺设集水管道，内径为8cm，收集的淤泥渗滤液排入集水井中(自然处理的淤泥)。运行6个月后，淤泥的含水率由90％降至79％，淤泥渗滤液中的COD、TN、TP、氨氮、铜、汞、砷等污染物的浓度见表1，属于劣五类水，不能直接排放到河道中。
对比例3：
仅采用实施例1中的淤泥生态处理系统(不进行渗滤液深度处理)，处理后淤泥的含水率为47％，出水中的COD、TN、TP、氨氮、铜、汞、砷等污染物的浓度见表1，属于五类水，不能直接排放到河道中。
对比例4：
采用对比例2的淤泥填埋池和渗滤液深度处理系统，其余操作步骤与实施例1相同，处理后淤泥的含水率为79％，出水中的COD、TN、TP、氨氮、铜、汞、砷等污染物的浓度见表1，属于劣五类水，不能直接排放到河道中。
对比例5：
与对比例3相比，去掉淤泥生态处理系统的曝气装置，处理后淤泥的含水率为52％，出水中的COD、TN、TP、氨氮、铜、汞、砷等污染物的浓度见表1，属于五类水，不能直接排放到河道中。
表1不同处理后的渗滤液中污染物浓度
Figure PCTCN2020096913-appb-000001
将表1中实施例1和对比例2-4的数据进行换算，得到不同单元单独处理对污染物的去除效果，见表2。
表2不同处理后的渗滤液中污染物的去除效果
Figure PCTCN2020096913-appb-000002
由表1和2可知，对比例3中单独采用淤泥生态处理系统处理后的出水中污染物COD、TN、氨氮和砷的含量分别为27mg/L、2.1mg/L、1.3mg/L和0.092mg/L，相对于对比例2中，COD、TN、氨氮和砷的去除率分别为44.10％、51.16％、63.89％和34.29％；对比例4中采用淤泥填埋池和渗滤液深度处理系统处理后的出水中污染物COD、TN、氨氮和砷的含量分别为39.8mg/L、3.4mg/L、2.8mg/L和0.112mg/L，与对比例2相比，即单独采用渗滤液 深度处理系统处理后污染物COD、TN、氨氮和砷的去除率分别为17.60％、20.93％、22.22％和20％。本发明实施例1采用淤泥生态处理系统和渗滤液深度处理系统联合处理的出水中污染物COD、TN、氨氮和砷的含量分别为14.5mg/L、0.5mg/L、0.4mg/L和0.045mg/L，相对于对比例2中，污染物COD、TN、氨氮和砷的去除率分别达69.98％、88.37％、88.89％和67.86％，较单独采用淤泥生态处理系统和单独采用渗滤液深度处理系统效果之和(分别为61.70％、72.09％、86.11％和54.29％)更优越，说明添加淤泥生态处理系统和渗滤液深度处理系统在去除污染物COD、TN、氨氮和砷方面相互支持。
由此可见，采用本发明的一体化系统处理河道淤泥，通过植物的蒸腾和吸收、填料的过滤和吸附、及微生物降解的协同作用，以及曝气充氧的辅助作用，可有效实现淤泥的脱水和无害化、淤泥渗滤液的深度处理、以及部分河/湖水的净化。
对比例6：
参照《虹吸式出水断流形式在大型污水泵站中的应用》(文献)，虹吸管的充水流量(Q)为Q＝g 1/2×D 2.5×(0.53-0.17α/90°)，D为管径8cm，α为虹吸管上升段的水平角，实施例1考虑到占地的问题，将水平角设置为45°。实施例1虹吸管的充水流量为0.0025m 3/s，在对比例6中将虹吸排水系统中的驼峰型虹吸管替换成U型，虹吸管的充水流量为0.0020m 3/s。实施例1虹吸管的充水流量要大于对比例6，说明驼峰型虹吸管的虹吸效果更好。
虽然本发明已以较佳实施例公开如上，但其并非用以限定本发明，任何熟悉此技术的人，在不脱离本发明的精神和范围内，都可做各种的改动与修饰，因此本发明的保护范围应该以权利要求书所界定的为准。

Claims (11)

  1. 一种河湖淤泥就地处理的一体化滨岸带系统，其特征在于，该一体化系统依次由淤泥生态处理、虹吸排水、淤泥渗滤液深度处理三个子系统组成；所述淤泥生态处理系统自上而下设置植物、填料、曝气管和集水管，通气管与集水管相连；虹吸排水系统中的虹吸管为可伸缩式驼峰型；所述淤泥渗滤液深度处理系统包括第一级生态处理单元升流式湿地和第二级生态处理单元表面流湿地；所述淤泥生态处理系统的填料自下而上分层设置，包括排水层、过渡层、过滤层和覆盖层；所述排水层为厚度10-30cm、直径10-30mm的砾石；所述过渡层为厚度5-20cm、直径4-15mm的砾石；所述过滤层为厚度15-45cm、直径0.5-5mm的砾石或沸石或砂或陶粒或火山石中的一种；所述覆盖层为厚度5-15cm、直径8-20mm的砾石；淤泥生态处理系统种植挺水植物，淤泥渗滤液深度处理系统的升流式湿地种植挺水植物和湿生植物，表面流湿地种植挺水植物、浮叶植物和沉水植物。
  2. 根据权利要求1所述的一体化系统，其特征在于，淤泥生态处理系统的填料各层之间铺设土工布。
  3. 根据权利要求1所述的一体化系统，其特征在于，淤泥生态处理系统底部坡度为0.1％-0.3％；所述集水管为穿孔管，与通气管相连，管道内径为8-15cm，通气管高出池体15-30cm，用土工布分别将集水管与通气管包裹；所述曝气管紧邻集水管并设置在其之上。
  4. 根据权利要求1所述的一体化系统，其特征在于，虹吸排水系统中的虹吸管形状为驼峰型，上升段水平倾角为30-45°；虹吸管设计成伸缩式，可灵活调节虹吸管的高度为15-50cm，驼峰顶点高于淤泥生态处理系统集水管15-35cm，虹吸管出水水位低于集水管水位20-40cm，虹吸管内径为8-15cm。
  5. 根据权利要求1所述的一体化系统，其特征在于，淤泥渗滤液深度处理系统的第一级生态处理单元升流式湿地的填料自下而上分层设置，包括进水层、过滤层和排水层；所述进水层为厚度10-30cm，10-30mm直径的砾石；所述过滤层为厚度15-30cm，0.5-5mm直径的砾石或沸石或砂或陶粒或火山石中的一种；所述排水层为厚度10-30cm，10-30mm直径的砾石。
  6. 根据权利要求1所述的一体化系统，其特征在于，升流式湿地的穿孔进水管和排水管分别设置在进水层和排水层内，管道内径为8-15cm，两管的水位差为20-40cm，进水管的水位低于虹吸管驼峰顶点40-60cm。
  7. 根据权利要求1所述的一体化系统，其特征在于，淤泥渗滤液深度处理系统的第二级生态处理单元表面流湿地的水位与河道/湖泊相同。
  8. 根据权利要求1所述的一体化系统，其特征在于，淤泥生态处理系统和淤泥渗滤液深度处理系统的池底及池壁铺设PE防渗膜，各层填料之间铺设土工布。
  9. 一种应用权利要求1-8任一所述一体化系统处理淤泥的方法，其特征在于，所述方法具体为：
    (1)淤泥生态处理：将河道和湖泊含水率高于70％的淤泥，以50-80kg干物质/(m 2·a)的负荷投加，分层平铺在淤泥生态处理系统的覆盖层之上，每隔30-60天投加一次，每次投加厚度不超过15cm，至池体填满为止，填充的最终高度为0.5-1.2m，含水率降至50％以下进行清除，淤泥生态处理系统内部配置通气管和曝气管，曝气间隔周期为15-30天，曝气量为50-100mL/min，曝气时间为1-2天，实现淤泥的脱水和无害化；
    (2)通过虹吸排水系统将淤泥生态处理系统底部集水管收集的渗滤液排到淤泥渗滤液深度处理系统；
    (3)在淤泥渗滤液深度处理系统中，渗滤液依次经过升流式和表面流湿地的两级生态处理，出水可以达标排入河道或湖泊，水量不足时河/湖水可以进入表面流湿地，实现部分河/湖水的净化。
  10. 根据权利要求9所述的方法，其特征在于，淤泥生态处理系统种植挺水植物，淤泥渗滤液深度处理系统的升流式湿地种植挺水植物和湿生植物，表面流湿地种植挺水植物、浮叶植物和沉水植物。
  11. 权利要求1-8任一所述的一体化系统在淤泥处理中的应用。
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