JP7281251B2 - Broad-Spectrum Matrix of Pollutant Effluent Adsorbent Compounds and Methods of Use - Google Patents

Description

CROSS-REFERENCE TO RELATED APPLICATIONS This application is a continuation-in-part of U.S. patent application Ser. 62/029,044 and the benefit of U.S. Provisional Application No. 62/133,791, filed March 16, 2015. The entire disclosure of the above application is hereby incorporated by reference.

This application relates generally to industrial emission control systems and methods, and equipment used in such systems, and methods of removing pollutants from gaseous and non-gaseous emissions. Emissions control systems may be used as permanent, fixed on-site systems, or trucks, trailers, rail cars, barges, and other similar structures capable of transporting and/or relocating the system from one point of use to another. It is possible to build on things. Additional fields of application relate to marine ship waste and/or deballasting from ships such as military ships, cargo ships, tankers, cruise ships.

This section presents background information related to the disclosure of this application that is not necessarily prior art.

Industries in many sectors of the economy produce more than one type of emissions. Such emissions can be divided into two basic groups, one gaseous and the other non-gaseous. Emissions in the gas group and non-gas group emissions often contain hazardous pollutants. Emissions in the gas group may be exhaust gases generated by coal-fired plants or natural gas-fired installations. Effluents in the non-gas group may be liquid, sludge-like or slurry-like materials. Neutralize, capture, collect, remove, dispose of, and/or take some form of action to neutralize, capture, collect, remove, dispose of, and/or otherwise remove hazardous contaminants when levels of hazardous contaminants in emissions reach and/or exceed acceptable limits. It must be properly sealed by means.

Many industries rely on burning fuel as a means to accomplish some aspect of their respective methods. For example, as a first example, steel mills burn and/or melt metal during metal forming, extrusion and other metal casting processes. Methods used within this metal industry involve operations that release powders as metal vapors and ionized metals. Pollutants harmful to the environment, plants, animals and/or humans are released into the air via metal vapors. To a greater or lesser extent, hazardous contaminants in this metal vapor and/or metal vapor compounds must be collected and properly disposed of. As a second example, mining operations for precious metals such as gold, silver and platinum also generate metals, metal vapor emissions and powders containing heavy metal contaminants, which must be captured, collected and properly disposed of. If not, it is considered harmful. As a third example, industries that burn natural gas produce effluents that often contain high levels of pollutants that are considered hazardous if not captured, collected and properly disposed of. As a fourth example, energy producers who use coal as a combustible consumable to produce steam in boilers that run electrical generators may produce metal vapors and metal compounds that are considered dangerous to the environment, plants, animals and humans. Generates significant amounts of emissions containing Among other harmful pollutants, metal vapor emissions often contain mercury (Hg).

Because of the global jet stream pattern, airborne metal vapor emissions can be transported from one country and deposited in another. For example, much of the mercury emissions originating in China and/or India may actually end up in ocean waters in and/or between the United States. Similarly, much of the mercury-bearing emissions generated in the United States may actually be deposited in the oceans of Europe and/or in between. Completing this cycle, mercury-bearing emissions originating in Europe may actually deposit in China and/or India. Mercury and other toxic pollutants in effluents generated from industrial processes are therefore a global problem of global significance that requires global efforts to be resolved.

National and international regulations, rules, limits, fees, oversight, and many more stringent laws under revision have been proposed and/or implemented against those that generate such emissions. Regulations and/or limits for hazardous emissions vary from country to country around the world. However, for example, one country may provide other countries with measures to reduce hazardous emissions generated by emissions producers in that country, even if the emissions may be deposited in another country. It is difficult, if not impossible, to enact controls that would encourage (let alone force) controls to take.

Japan has been a global leader in reducing mercury production and mercury-containing emissions since the 1970s. Japan is enacting rules that affect how the larger global community should respond to environmental issues specifically related to mercury production. Japan's efforts to promote international mercury legislation are aimed at preventing mercury-related diseases. In addition to Japan, the United States also has some of the world's most stringent and restrictive laws and regulations, enforced by the United States Environmental Protection Agency (EPA). One of the most harmful contaminants in metal vapor emissions is mercury. With the goal of reducing the amount of mercury emitted by coal-fired plants by 91% by 2016, the EPA has established a "Mercury and Toxic Air Pollutants Standard" that regulates mercury emissions from various public utilities across the United States. ” and other new revision programs. Although these imposed regulations are an ongoing subject of political and legal debate, the issue of hazardous pollutants that must be disposed of remains overshadowed.

Enforcement of the law by the EPA does not extend to producers of hazardous emissions within industrial countries such as India, China and other foreign countries. The United Nations (UN) is therefore attempting to put pressure on its member states to reduce emissions of hazardous metal vapors. Representatives of at least 140 Member States have agreed to reduce global mercury emissions under the treaty, which entered into force in 2013. However, although global improvements have been observed in some countries, the expansion of the newly industrialized countries appears to have greatly outpaced the progress of mitigation efforts.

Focusing on mercury does not reduce the harmful effects of other contaminants in metal vapor emissions, but mercury is potentially the most prevalent and most harmful to animals and humans. Mercury is a natural element present in plants, soils and animals around the world. However, human-industrial processes have increased the accumulation of mercury and/or mercury deposits far beyond naturally occurring levels. On a global scale, the total amount of mercury released by human activities is estimated to be 1,960 metric tons per year. This figure was calculated from data analyzed in 2010. Globally, the largest contributors to this particular type of emissions are coal burning (24%) and gold mining (37%) activities. In the United States, coal burning accounts for a higher proportion of emissions than gold mining activities.

For animals and humans, the major problem with mercury exposure is that mercury is a bioaccumulator. Therefore, any amount of mercury ingested by a fish or other animal remains (i.e. accumulates) in that animal and is transferred to humans or, if the former is ingested by the latter, to other animals. . Furthermore, mercury is not excreted from the body of the ingesting host. Larger predators that live the longest and/or prey on large numbers of other animals in the food chain are most at risk of excess mercury accumulation. Humans who eat mercury-containing animals (particularly fish) are exposed to a wide range of well-known medical problems, including neurological disorders and/or reproductive problems.

There are three main types of mercury emissions: Anthropogenic releases, re-releases and natural releases. Anthropogenic releases are largely the product of industrial activity. Anthropogenic sources include industrial coal-fired plants, natural gas-fired plants, cement production plants, petroleum refineries, chlor-alkali industries, vinyl chloride industries, mining operations and refining operations. Re-release occurs when soil-deposited mercury is redistributed by floods or forest fires. Mercury absorbed and/or deposited in soil is released back into the water by storm runoff and/or flooding. Soil erosion contributes to this problem. Forest fires (whether naturally occurring, arson, or intentional deforestation fires) re-release mercury into air and/or water sources and deposit elsewhere. Natural emissions include volcanoes and geothermal vents. Approximately half of all mercury released into the atmosphere is estimated to come from natural events such as volcanoes and geothermal vents.

As noted above, coal-burning plants release large amounts of mercury and other pollutants into the environment each year. Accordingly, numerous efforts are currently underway to reduce the amount of harmful pollutants in flue gas emissions generated by coal-fired plants. Many coal-fired plants in the United States are equipped with emission control systems that capture, contain, and/or regenerate hazardous elements such as mercury. In a coal-fired plant, coal is burned to boil water, convert water to steam, and drive a generator. Flue gas emissions from coal combustion are often sent through a conduit system and/or a jet dryer system to a fluid gas desulfurization unit to remove some emissions from the flue gas and sulfur dioxide (SO2 ) and hydrogen chloride (HCl) are removed. A conventional conduit system then directs the flue gas stream to a wet/dry scrubber where more sulfur dioxide, hydrogen chloride and fly ash are removed. The flue gas stream is passed through a baghouse where particles are separated from the air stream in the flue gas, similar to a domestic vacuum cleaner bag. The flue gas passes through a filter-like bag having a porosity that allows air flow but impermeable to larger particles moving in the air flow. The surface of the filter bag is agitated and/or washed to collect the trapped particles and make them ready for disposal. Generally, these deposits are themselves hazardous emissions and must be disposed of. The remainder of the flue gas that has passed through this type of emission control system passes through a tall chimney and is discharged to the atmosphere.

A problem with this type of emission control system is that it is not practically effective at capturing and/or collecting heavy metals such as mercury contained in metal vapors and vaporous metal compounds. Because coal combustion systems burn coal at relatively high temperatures, approximately 1500 degrees Fahrenheit, mercury turns into nano-sized particles that can pass through even the most efficient filter systems. As a result, large amounts of airborne mercury and other harmful pollutants are released into the atmosphere.

Several known systems have been developed to meet this challenge to capture and collect mercury from coal combustion systems and/or other sources of emissions. These fall into one of three categories.

The first category is a group of methods and/or systems that capture mercury by injecting sorbents into the flue gas stream. Besides noble metals, the most common adsorbent material is activated carbon, which is often halogenated with bromine. Injection of the sorbent into the flue gas is to capture pollutants in one and/or a combination of the following conventional emission control systems. An electrostatic precipitator, a fluidized gas desulfurization system, a washer system, or a fiber filter system. There are several variations of these systems that require injecting activated carbon at various points in the emissions control system after coal combustion. Some exemplary methods and/or systems in the first category are disclosed in U.S. Pat. 7,704,920, 7,141,091, 6,905,534, 6,712,878, 6,695,894, 6,558,454, 6,451,094, 6,136,072, 7, 618,603, 7,494,632, 8,747,676, 8,241,398, 8,728,974, 8,728,217, 8,721,777, 8,685,351, and 8,029 , 600. All of the methods and/or systems described in these exemplary patents generate hazardous and/or unusable waste and thus have their own disposal problems. Additionally, these methods and/or systems are generally not economically viable and fail to meet emission regulations imposed by the EPA and/or other agencies.

A major problem with the methods and/or systems of the first category of known solutions is that the use of activated carbon is expensive and inefficient. The initial cost of the activated carbon is increased because only approximately 10% of the activated carbon interacts with the metal vapor as it passes through the system. Therefore, as much as 90% of the expensive activated carbon is wasted into the flue gas, primarily as carbon monoxide (CO) and/or carbon dioxide (CO2). Another problem is that activated carbon often produces fly ash that is unsuitable as a raw material for the manufacture of concrete or other filler-requiring industrial products. Selling fly ash doesn't make a lot of money, but in large quantities, this coal-burning plant by-product can actually be an additional source of income. By-product quantities of fly ash that are unsuitable for use as fillers in concrete must be classified as hazardous waste, thus incurring disposal costs. On the other hand, by-product quantities of fly ash that are suitable as fillers in concrete are not classified as hazardous waste and are therefore a salable product and do not incur disposal costs.

Another problem with the known solution methods and/or systems of the first category is that as much as 10% of the mercury in the flue gas is not removed and is released into the environment. This percentage is high compared to the mercury emissions allowed by the EPA and other agencies. Therefore, none of the methods and/or systems of the first category of known solutions meet current regulations for the collection and/or capture of mercury in coal-fired plants or similar industrial applications.

Yet another problem with using activated carbon is that carbon monoxide and/or carbon dioxide is produced and released into the atmosphere when activated carbon is burned. In the United States alone, it is estimated that as many as 2.8 billion tons of carbon dioxide are generated annually by using activated carbon in coal-burning plants. Worldwide, it is estimated that as much as 14.4 billion tons of carbon dioxide are generated annually from the use of activated carbon in coal-fired plants. In addition, activated carbon is less effective at removing mercury from other forms of non-gaseous emissions, so alternative methods must be used.

The second category is methods and/or systems for pre-treating coal fuel prior to combustion to reduce mercury levels in coal fuel. Some exemplary methods and/or systems in this second category are disclosed in U.S. Pat. , 8,062,410 and 7,987,613. All of the methods and/or systems described in these exemplary patents produce large amounts of unusable coal, which is also considered hazardous waste. As a result, methods and/or systems of the second category of known solutions are ineffective and expensive to implement. Additionally, coal pretreatment often requires large amounts of capital and physical space, making it impractical to retrofit many existing emission control systems with the necessary equipment.

The third category is a group of methods and/or systems that inject catalyst into emissions control equipment upstream of the activated carbon injection system. The catalysts in these methods and/or systems ionize mercury to facilitate its collection and removal from flue gases. However, the efficiency of such methods and/or systems is low, leading to high operating costs, and methods and/or systems of the third category of this known solution are not cost effective. Examples of this third category are described in US Patent Nos. 8,480,791, 8,241,398, 7,753,992, and 7,731,781. In addition to these examples, US Pat. No. 7,214,254 discloses a method and apparatus for regenerating expensive adsorbent materials using microwave ovens and fluidized bed reactors. This method selectively evaporates mercury from the sorbent, at which point it can be captured by special filters or concentrated for collection. Due to the use of microwave ovens, this method is not practical for large-scale commercial applications and is therefore only useful for regenerating expensive adsorbents. Another example is shown in U.S. Patent Application No. 2006/0120935, in which one of several substrate materials is used to impart an affinity to mercury for combustion as the flue gas passes through an emissions control facility. A method for removing mercury from flue gas is disclosed. This method is also impractical for large-scale commercial use.

Accordingly, current emission control systems and methods generally operate by moving hazardous pollutants from gaseous emissions to non-gaseous emissions, thereby creating additional emissions management problems.

While many laws and regulations focus on metal vapor emissions, slurry and/or slurry emissions, sludge and/or sludge emissions, liquid and/or liquid emissions, and other types of emissions. Effluents containing other forms of hazardous pollutants, such as, should not be overlooked. All types of effluents listed also require treatment to neutralize, capture, collect, remove, dispose of, and/or appropriately seal in some way the hazardous contaminants they contain. there's a possibility that. Historically, the most cost-effective and most widely used hazardous pollutant removal process has employed activated carbon (in some form) through which the effluent passes. Accordingly, the demand for activated carbon in the United States is projected to exceed £1 billion annually and grow annually through 2017, costing industry in excess of $1 to $1.50/lb. This equates to approximately $1 billion annually. Much of the projected increase in activated carbon demand will be influenced by the implementation of regulations promulgated by the EPA requiring utilities and manufacturers to update their coal-fired plants to comply with stricter requirements.

In addition to stricter gas emissions regulations, the EPA has also added stricter regulations on non-gaseous emissions through the Clean Water Act, which must be fully compliant by 2016. Composite regulations tightened for all types of emissions cover multiple types of emissions produced by a variety of different industries. Utilities that burn fuel to produce electricity, such as power utilities, generate primary gaseous emissions that contain hazardous pollutants. In accordance with industry standards, these gaseous effluents are exposed to activated charcoal to capture sufficient quantities of noxious contaminants to bring the contaminants of the gaseous effluents to below acceptable limits. The process of removing hazardous pollutants from the gaseous emissions produced by burning this fuel produces secondary non-gaseous emissions, which are liquid or slurry materials containing hazardous pollutants. Hazardous pollutants in this secondary non-gaseous effluent must also be captured and/or appropriately sealed to prevent release of this hazardous pollutant into the environment. Both primary gaseous emissions and secondary non-gaseous emissions require means to adequately capture and/or regenerate and/or contain sufficient hazardous pollutants to comply with environmental standards. and The industrial costs of known methods capable of removing hazardous pollutants from secondary non-gaseous emissions are almost prohibitive, and some industries are forced to invest in equipment if the costs cannot be added to the consumer. forced to close.

According to some practices, non-gaseous effluents that are considered hazardous because they contain high levels of contaminants are disposed of and stored in ponds, piles or dry beds for long periods of time. While such practices isolate hazardous pollutants, they are costly and consume land without neutralizing the hazardous pollutants themselves, which can result in environmental problems at the camp. have a nature. One example of non-gaseous emissions is fly ash, which is a natural product of burning coal. Fly ash is essentially identical in composition to volcanic ash. Fly ash contains trace concentrations (i.e., trace amounts) of many types of heavy metals and other known harmful and toxic contaminants (e.g., mercury, beryllium, cadmium, barium, chromium, copper, lead, molybdenum, nickel, radium, selenium, thorium, uranium, vanadium, zinc). By one estimate, 10% of the coal burned in the United States consists of non-combustible material, which becomes ash. Therefore, the concentration of harmful trace elements in coal ash is ten times higher than the concentration of these elements in the original coal.

Fly ash is considered a pozzolanic material and, when mixed with calcium carbonate, forms a cementitious material that agglomerates with water and other compounds to produce concrete mixtures suitable for roads, airport runways and bridges. has long been used in the production of Fly ash produced in coal-fired plants is flue ash consisting of ultra-fine particles that rise with the flue gas. Ash that does not rise is often called bottom ash. Early coal-fired plants simply released fly ash into the atmosphere. In recent years, environmental regulations have created a need to install emission control mechanisms to prevent fly ash from being released into the atmosphere. Many plants use electrostatic precipitators to trap fly ash before it reaches the chimney and escapes to the atmosphere. Bottom ash is usually mixed with captured fly ash to form what is known as coal ash. Fly ash typically contains higher levels of toxic contaminants than bottom ash, whereby mixing bottom ash and fly ash produces a proportionate level of toxic pollution that complies with many standards for non-gaseous emissions. Substance is produced. However, future standards may redefine fly ash as a hazardous material. If fly ash is redefined as a hazardous material, it will no longer be available for use in cement, asphalt manufacturing and other widely used applications. According to one study, a ban on fly ash use in concrete manufacturing would increase costs by more than $5 billion per year in the United States alone. This cost increase is a direct result of replacing fly ash with another, more expensive material. In addition, due to its unique physical properties, there are no other known suitable direct replacements for fly ash as a cement additive.

More than 130 million tons of fly ash are produced annually in more than 450 coal-fired power plants in the United States, according to the report. One report estimates that only 40% of fly ash is recycled, which is 52 million tons/year of fly ash recycled, while 78 million tons/year remain in slurry ponds and mountains. Indicates that it is reserved. Fly ash is typically stored in wet slurry ponds to reduce entrainment of airborne particles and contaminants out of bulk reservoirs into the atmosphere or surrounding environment. In addition to the airborne release of bulk stored fly ash, there is also the risk of damage and/or failure of the containment systems necessary to contain fly ash for extended periods of time. In a notorious 2008 failure in Tennessee, the levee of a wet fly ash reservoir collapsed, spilling 5.4 million cubic yards of fly ash. This overflow of fly ash destroyed several homes and polluted nearby rivers. Cleaning costs are undetermined at the time of filing this application and may exceed $1.2 billion.

As another example, non-gaseous effluents may be found as a by-product of the wastewater generation system of conventional coal-fired plants. A typical wastewater generation system produces large amounts of water from boilers and water cooling processes. These bulk effluents contain relatively low levels of contaminants and are used to dilute other effluent streams containing higher levels of contaminants. The contaminated effluent stream, which is normally discharged from the washing unit, is diluted by bulk effluent from the boiler and/or cooling water process and then treated with lime in large continuous mixing tanks to form gypsum and then It is pumped to the sedimentation pond. During this process, certain amounts of mercury and other heavy metals are incorporated into the gypsum and stabilized for use in wallboard and cement. This gypsum is generally considered non-leaching and is not considered a contamination. However, the water from the sedimentation basin is usually discharged into a drainage ditch. Current regulations allow for this ongoing discharge, but forthcoming regulations must designate certain pollutants and/or certain levels of these pollutants as hazardous pollution. is proposed.

For the removal of mercury and heavy metals from non-gaseous industrial effluent streams, carbonates, phosphates or sulfates are often used to reduce hazardous pollutants to low residual levels. One known method of removing mercury and other hazardous pollutants from industrial wastewater streams is chemical precipitation reactions. Another known method uses ion exchange. One of the major problems with chemical precipitation reactions and ion exchange methods is that when the amount of contaminants is high (e.g. when processing fly ash slurry effluents), these methods become more demanding on non-gaseous effluents. This means that it cannot fully comply with EPA regulations for

Another source of polluted non-gaseous emissions is marine ship waste discharges and ballast water discharges. Commercial vessels such as cargo ships and tankers have both waste and ballast discharges. Recreational cruise ships also have wastewater to treat at port. Military and escort vessels also have considerable amounts of waste water.

Substantial wastewater is also produced by offshore drilling operations. On-site treatment of effluents at offshore drilling facilities is significantly less expensive than transporting the wastes to land for treatment. Therefore, efficient filtration of marine waste prior to discharge into the sea is necessary in order to maintain adequate and acceptable ecological regulations. Virtually all uses of polluted effluents differ in the type and/or specific concentration of pollutants in the effluent. Therefore, there can be no one-size-fits-all approach to obtaining preferred adsorbents optimized for all conceivable pollutant effluent applications. There is a need to provide application-specific sorbent solutions to optimize effective emissions control based on the specific contaminants in the emissions. Additionally, there is a need to be able to adjust the sorbent application during use to accommodate changes in the level and/or type of contaminants in the effluent.

There are also various known commercial emission control methods and systems sold under different trade names for treating secondary non-gaseous emissions. A treatment process known under the trade name Blue PRO is a reactive filtration process that uses co-precipitation and adsorption to remove mercury from secondary non-gaseous effluents. Another treatment method, known under the trade name MERSORB-LW, uses powdered coal-based sorbents to remove mercury from secondary non-gaseous effluents by co-precipitation and adsorption. Another treatment method, known as Chloralkali Electrolysis Wastewater, removes mercury from the secondary non-gaseous effluent during the electrolytic production of chlorine. Another treatment method uses absorption kinetics and activated carbon derived from manure wastewater to remove mercury from secondary non-gaseous effluents. In another treatment method, polyethyleneimine-modified porous cellulose alone is used as an adsorbent to remove mercury from secondary non-gaseous effluents. Another treatment method uses microorganisms to remove mercury from the secondary non-gaseous effluent during enzymatic reduction. Yet another treatment method, known under the trade name MerCURxE, uses a chemical precipitation reaction to treat contaminated liquid non-gaseous effluents.

A common treatment method with some emissions control systems is to dilute pollutants instead of removing them from the emissions. As a result, if the PPM level of a contaminant in an effluent exceeds the allowable range, instead of removing the contaminant to reduce the level, additional A non-fouling volume is added to the effluent to reduce the PPM level to an acceptable level. There is a significant need to eliminate such dilution practices by providing an effective emission control method that not only lowers the PPM levels of pollutants, but also removes pollutants from emissions.

This section provides a general summary of the disclosure and is not intended to be a comprehensive disclosure of its full scope or all features.

In one aspect of the present disclosure, an apparatus for removing contaminants from effluent is disclosed. The device comprises an inverted venturi-shaped housing. The housing has an inlet portion into which the discharged matter flows in at a predetermined inlet flow velocity, an outlet portion through which the discharged matter is discharged at a predetermined outlet flow speed, and a portion disposed between the inlet portion and the outlet portion of the housing. and an enlarged diameter portion for trapping contaminants in the air. The inlet section, outlet section and enlarged diameter section of the housing are arranged in fluid communication with each other. Additionally, the inlet portion of the housing has an inlet cross-sectional area, the outlet portion of the housing has an outlet cross-sectional area, and the enlarged diameter portion of the housing has an enlarged diameter cross-sectional area. Due to the inverted venturi shape of the housing, the enlarged diameter cross-sectional area is greater than the inlet cross-sectional area and the outlet cross-sectional area. Due to the shape of the housing, the effluent entering the enlarged diameter portion of the housing is decelerated and passes through the enlarged diameter portion of the housing at a lower speed relative to the speed at which it passes through the inlet and outlet portions of the housing. . Since the flow of effluent is slowed at the enlarged diameter portion of the housing, the residence time of the effluent in the enlarged diameter portion of the housing increases. The device also has a reactant mass disposed within the enlarged diameter portion of the housing. The reactant mass has a reactive outer surface positioned to contact the effluent. Additionally, the reactant mass contains an amalgam-forming metal on the outer reaction surface. The amalgam-forming metal in the reactant mass chemically bonds with at least a portion of the contaminants in the effluent that reach the reactive outer surface of the reactant mass through the enlarged diameter portion of the housing.

In another aspect of the present disclosure, an emissions control method is disclosed for removing pollutants from gaseous emissions. This method comprises the following steps. burning fuel in a furnace to produce a pollutant-laden gaseous effluent, passing the gaseous effluent through an electrostatic precipitator, and using the electrostatic precipitator to remove particulate pollutants from the gaseous effluent; passing the gas effluent through a fluidized gas desulfurization unit to remove sulfur dioxide contaminants from the gaseous effluent using the fluidized gas desulfurization unit; and passing the gaseous effluent through a fiber filter unit. and removing a second portion of the particulate contaminants from the gas effluent using the fiber filter unit. The method may include passing the gaseous effluent through a reverse venturi device and removing heavy metal contaminants from the gaseous effluent using the reverse venturi device. Passing the gaseous effluent through a reverse venturi device and removing heavy metal contaminants from the gaseous effluent using the reverse venturi device includes passing the gaseous effluent through a reactant mass disposed within the reverse venturi device. . The reactant mass contains amalgam-forming metals that chemically bond with heavy metal contaminants in the gaseous effluent. Thus, heavy metal contaminants are trapped in the reverse venturi device as they combine with the amalgam-forming metals in the reactant mass. The method further includes directing the gaseous effluent to a chimney that releases the gaseous effluent into the surrounding atmosphere.

In yet another aspect of the present disclosure, an emission control method for removing contaminants from non-gaseous emissions is disclosed. The method comprises sedimenting a non-gaseous effluent containing contaminants in a sedimentation basin to remove a portion of the contaminants in the non-gaseous effluent, dewatering a first portion of the non-gaseous effluent in the sedimentation basin, Using the dewatered by-product in a secondary industrial process, removing a second portion of the non-gaseous effluent from the settling pond and subjecting the second portion of the non-gaseous effluent to a dry waste treatment. The method may further include the step of sending a third portion of the non-gaseous effluent in the sedimentation basin to a treatment vessel containing the adsorbent. The adsorbent contains amalgam-forming metals that chemically bond with heavy metal contaminants in the third portion of the non-gaseous effluent. The adsorbent thus captures heavy metal contaminants in the treatment vessel as the heavy metal contaminants chemically bond with the amalgam-forming metals in the adsorbent. The method may further comprise the step of directing the non-gaseous effluent from the treatment vessel to a drain.

The apparatus and methods described herein have numerous advantages over known emission control systems and methods. The apparatus and methods disclosed herein significantly reduce and/or eliminate the need for activated carbon in coal burning emissions. Currently, the initial cost of amalgam-forming metals and adsorbents in the reactant mass disclosed herein is only $1 to $1.5 more than the pound acquisition cost of activated carbon. expensive. However, since the amalgam-forming metals can be reactivated and the hazardous contaminants collected and reused, the increased costs are temporary costs. As a result, the first-year cost of using amalgam-forming metals, including the materials disclosed herein, including reclamation and reactivation costs, is 1.5 times the annual cost of activated carbon, or $1.5 billion across the United States. estimated to be as high as However, estimated annual costs after the first year of investment only include annual regeneration and revitalization costs, which are estimated at $250 million across the United States. Thus, over ten years, the first year cost to American industry is $1.5 billion, with regeneration and revitalization costs of $250 million each for the next nine years, for a total ten year cost of $37.7 billion. $500 million. This figure is low compared to the over $10 billion cost of using activated carbon, and a significant cost savings of $6.5 billion over 10 years is achievable.

In addition to significant cost savings, the present apparatus and methods are more efficient in removing hazardous pollutants from gaseous and non-gaseous emissions compared to known emission control systems and methods. These improvements are significant enough to enable industry to meet and/or exceed anticipated regulatory requirements, which are economically feasible with current technology. Impossible. Therefore, the apparatus and methods of the present application have the ability to continue to use fly ash even when regulations reclassify fly ash as a hazardous material, thereby enabling the construction industry, commercial power generation industry, and others. Significant cost increases can be prevented in industries that produce non-gaseous ash by-products.

The disclosed apparatus and method also greatly reduce, if not eliminate the use of activated carbon in removing hazardous pollutants from gaseous effluents. Reducing the use of activated carbon in emission control systems is estimated to reduce annual carbon dioxide emissions by as much as two billion tons in the United States alone.

In another aspect of the present disclosure, an emissions control method is disclosed for removing pollutants from gaseous emissions. This method comprises the following steps. Injecting a potentially contaminated gaseous effluent source into the system, passing the effluent through an application-specific prefilter, if necessary, passing the effluent through a fluidized bed in an inverted venturi geometry, Optionally, passing the effluent through an application specific post-filter and then exiting the effluent from the system. The purpose of venting the system may be either suitable purposeful disposal of the uncontaminated gas stream and/or environmentally controlled reduction and/or release.

Specifically, a fluidized bed in an inverted venturi geometry provides a constant length-to-diameter flow rate for optimal restricted residence time of the gaseous effluent as it passes through a special adsorbent contained within the device. It may be sized to have a ratio. Trial and error has shown that the optimum length to diameter ratio for fluidized bed vessels is between 2.9:1 and 9.8:1, preferably 4.4:1, for example. Thus, in one exemplary preferred embodiment, if the diameter is 4.5 feet, then the length is 19.8 feet, giving a length to diameter ratio of 4.4:1.

Another feature of the exemplary inverted venturi shaped fluid bed apparatus for gas effluent is that it has a generally curved, outwardly projecting convex end when viewed from either end of the exterior of the vessel. . Tests in an embodiment of a system with a fluidized bed have shown that the flow of gaseous effluent returns to random on its own, minimizing cavitation turbulence and thus maximizing intimate contact, thus increasing the amount of stagnation in contact with the adsorbent. The time has come. The generally curved, outwardly projecting convex ends allow relatively smooth return flow at both ends of the fluidized bed and also minimize cavitation turbulence in the gaseous effluent. Turbulence associated with cavitation through filters is known to impede and/or disrupt flow. A longer residence time in the fluidized bed is desired for optimal contaminant capture and removal from the gaseous effluent. However, for turbulent flow with cavitation, extended residence time is not optimized. Various baffles and other application-specific flow restriction obstructions can be incorporated into the fluidized bed enclosure.

In yet another aspect of the present disclosure, an emission control method for removing contaminants from non-gaseous emissions is disclosed. This method comprises the following steps. Injecting a potentially contaminated non-gaseous emission source into the system, passing the effluent through an application-specific prefilter, if necessary, passing the effluent through a fluidized bed in an inverted venturi configuration, if necessary passing the effluent through an application-specific post-filter, depending on requirements, and then venting the effluent out of the system. The purpose of exiting the system may be either suitable purposeful disposal of the uncontaminated non-gas stream and/or environmentally controlled reduction and/or release.

Specifically, the fluidized bed in an inverted Venturi configuration has a length-to-diameter ratio that optimizes the restricted residence time of the non-gaseous effluent as it passes through a special adsorbent contained within the device. It may be sized to have a ratio. Trial and error has shown that the optimum length to diameter ratio for fluidized bed vessels is between 2.9:1 and 9.8:1, preferably 4.4:1, for example. Thus, in one exemplary preferred embodiment, if the diameter is 4.5 feet, then the length is 19.8 feet, giving a length to diameter ratio of 4.4:1.

Another feature of the exemplary non-gaseous effluent inverted venturi fluid bed apparatus is that it has a generally curved, outwardly projecting convex end when viewed from either end of the exterior of the vessel. be. Tests in an embodiment of a system with a fluidized bed show that the flow of non-gaseous effluent returns to random on its own, minimizing cavitation turbulence and thus maximizing intimate contact with the adsorbent. residence time was determined. The generally curved, outwardly projecting convex ends allow for relatively smooth return flow at both ends of the inverted venturi shaped fluidized bed and also minimize cavitation turbulence of the non-gaseous effluent. Turbulence associated with cavitation through filters is known to impede and/or disrupt flow. For optimal contaminant capture and removal from non-gaseous effluents, it is desirable to extend the residence time in the inverted venturi fluidized bed. However, for turbulent flow with cavitation, extended residence time is not optimized. Various baffles and other application-specific flow restriction obstructions can be incorporated into the fluidized bed enclosure.

In another aspect of the present disclosure, an inverted venturi fluidized bed system for gaseous and/or non-gaseous effluent is removable from the vessel of the inverted venturi fluidized bed to collect contaminants from the adsorbent. is. In this case, the captured contaminants can be properly disposed of and/or recycled for appropriate industrial use. After the adsorbent has been regenerated and/or activated, it can be rearranged into the fluidized bed for further use within the system. In order to maintain the amount of adsorbent in the fluidized bed, a built-in inlet of adsorbent may be provided.

According to another aspect of the present disclosure, the inverted venturi-shaped fluidized bed maintains the disclosed length-to-diameter ratio characteristics and generally curved, outwardly projecting convex end characteristics, while maintaining individual It can be significantly lighter for consumer use or upsized for very large commercial use. Permanent systems include, but are not limited to, ground-based site systems and/or field assembly on escort or military vessels and consumer cruise ships. Other possible field-assembled system applications include industrial coal-fired plants, natural gas-fired plants, cement production plants, petroleum refineries, chlor-alkali industries, vinyl chloride industries, mining operations and refining operations, among others.

In another aspect of the present disclosure, an exemplary contaminant removal system includes reconfigurable articulated components. Each system component can be isolated, bypassed, embedded, and/or reconfigured to suit the requirements of a particular application. This system comprises a fluidized bed device incorporating a tilting mechanism.

The tilting mechanism is fixed to a cradle deck arranged parallel to the horizontal plane. The tilting mechanism changes the orientation of the axis through the center of the fluidized bed from an orientation parallel to the cradle deck to an orientation generally transverse to the cradle deck.

Tilting can be accomplished by any number of conventional mechanical coupling methods similar to how dump truck tilting beds work. Tilt mechanisms are typically powered by pneumatics, hydraulics, electric motors, and/or combinations thereof. Accurate positioning and tilt control is typically achieved through programmable logic control.

Trial and error has shown that the tilt mechanism works best for gaseous and non-gaseous emissions with total sweep angles up to 96 degrees. The total sweep angle is specifically limited to 96 degrees to allow the fluidized bed apparatus enclosure to tilt up to the full 90 degrees and also parallel and cross the cradle deck. It is positionable in a fixed orientation at any tilt angle that increments between (transverse) states.

The tilting mechanism tilts the enclosure of the fluidized bed apparatus −2.5 degrees from a parallel orientation with respect to the gantry deck and an additional 3.5 degrees from a transverse orientation with respect to the gantry deck. (93.5 degrees) to achieve a total sweep angle of 96 degrees.

In an example application of the disclosure to a contaminated gaseous effluent, the tilt mechanism reciprocally oscillates the fluidized bed apparatus housing such that the oscillating sweep angle for the gaseous effluent is 5.5 degrees. Specifically, the tilt mechanism orients the enclosure of the fluidized bed apparatus at a gaseous effluent treatment angle (0 degree tilt angle) that is substantially horizontal and parallel to the cradle deck. The tilting mechanism tilts the fluidized bed apparatus between a first oscillation angle that is +3 degrees above the horizontal orientation of the enclosure relative to the gantry deck and a second oscillation angle that is -2.5 degrees below the horizontal orientation of the enclosure relative to the gantry deck. to vibrate the housing of the In this orientation, the contaminated gaseous effluent is passed through the fluidized bed apparatus and monitored. The housing may be gradually tilted within the range of 5.5 degrees of oscillatory sweep angle to determine the optimum tilt angle for optimum restrictive flow.

In another application, the tilting mechanism is configured to continuously vibrate the housing of the fluidized bed apparatus within an oscillating sweep angle of 5.5 degrees so that the contaminated gaseous effluent flows through the fluidized bed apparatus. Provide a method of agitation as it passes through.

Through the practical application of methods of vibrational excitation by external equipment, ultrasonic vibration, fluidized bed apparatus housing rotation, radial rocking, axial rocking, and/or combinations thereof, gaseous emissions is applicable to the fluidized bed.

In another application of the present disclosure to contaminated non-gaseous effluent, the tilting mechanism reciprocally oscillates the housing of the fluidized bed apparatus with a non-gaseous effluent vibration sweep angle of 7.5 degrees. Specifically, the tilt mechanism orients the enclosure of the fluidized bed apparatus at a non-gaseous effluent treatment angle (tilt angle: 90 degrees) that is substantially vertical and transverse to the cradle deck. The tilt mechanism has a first swing angle (93.5 degrees) that is +3.5 degrees from the transverse orientation of the enclosure to the gantry deck and - from the transverse orientation of the enclosure to the gantry deck. Vibrate the housing of the fluidized bed apparatus through a second reciprocating angle (86 degrees) that is 4.0 degrees downward. In this orientation, contaminated non-gaseous effluent is passed through the fluidized bed apparatus and monitored. The housing of the fluidized bed apparatus may be gradually tilted within the non-gas oscillation angle of 7.5 degrees to determine the optimum tilt angle for optimum restrictive flow.

In another exemplary application, the tilting mechanism continuously vibrates the housing of the fluidized bed apparatus within a non-gas oscillation angle of 7.5 degrees so that the contaminated non-gas effluent flows into the fluidized bed apparatus. configured to apply an agitation method as it passes through the

By practically applying methods of vibrational excitation by external equipment, ultrasonic vibration, fluidized bed apparatus housing rotation, radial rocking, axial rocking, and/or combinations thereof, non-gas evacuation The method of further agitating the material is applicable to the fluidized bed apparatus.

In another application of the disclosure to more sludge-like and/or naturally aerated polluted effluents, the orientation of the fluidized bed apparatus enclosure is about 45 degrees to the gantry deck (45 degrees to horizontal). aeration sludge discharge treatment angle of 10.0 degrees. The tilting mechanism tilts the fluid bed unit housing at +/-5.0 degrees in either direction relative to the aerated sludge effluent treatment angle (between 40 and 50 degrees relative to the cradle deck). vibrate. In this orientation, the aerated, sludgy pollutant effluent is passed through the fluidized bed apparatus and monitored. The housing of the fluidized bed apparatus may be gradually tilted within a 10.0 degree oscillatory sweep angle to determine the optimum tilt angle for optimum restrictive flow.

In another application, the tilting mechanism continuously vibrates the housing of the fluidized bed apparatus within an oscillatory sweep angle of 10.0 degrees, and the aerated, sludge-like contaminated effluent passes through the fluidized bed apparatus. It is configured such that the agitation method is applied when

Aerated by practical application of methods of vibrational excitation by external equipment, ultrasonic vibration, rotation of the fluidized bed apparatus housing, radial rocking, axial rocking, and/or combinations thereof. A method of further agitating the sludgy polluted effluent is applicable to the fluidized bed apparatus.

The inlet for the gaseous effluent into the enclosure of the fluidized bed apparatus is provided independently from the inlet for the non-gaseous effluent. The outlet for gaseous emissions is provided independently from the outlets for non-gaseous emissions. By providing inlets and outlets for the various effluents, depending on the orientation of the fluidized bed apparatus housing, a more favorable tortuous flow path through internal obstructions within the fluidized bed apparatus housing may be created. can.

The fluidized bed apparatus also has additional holes for cleaning and/or replacing the adsorbent material. The adsorbent can be removed from the housing of the fluidized bed apparatus and washed. If the sorbent appears exhausted, it can be separated and disposed of. Contaminants may be separated from the adsorbent and transported for industrial recycling or proper disposal. The washed adsorbent may be returned to the fluidized bed apparatus housing along with replacement adsorbent to replace the depleted adsorbent.

In addition to being a permanent, purpose-built system, the system can also be configured as a portable system. Examples of portable systems include, but are not limited to, truck-mounted systems, barge-mounted systems, trailer-mounted systems, railcar systems. For portable system applications, in providing a bypass to a field-assembled system by providing a temporary emissions bypass for servicing, servicing, and/or repairing a permanently installed field-assembled system. Useful. Portable systems are also useful in implementing excess filtering capabilities in permanent field-assembled installations while the flow rate of contaminated effluent exceeds the capacity of permanent field-assembled systems.

There are numerous advantages of using the specialized adsorbents described herein with the disclosed apparatus and methods. In general, the ability of the effluent system disclosed by this sorbent to capture, contain and/or recycle mercury and other hazardous materials is previously not possible using known effluent control systems and methods. Another important advantage of the sorbents disclosed herein is that the sorbents can be used to treat both gaseous and non-gaseous effluents, thereby Many of the problems of known methods of treating polluted non-gaseous emissions, such as secondary emissions resulting from primary emission control treatments used, can be overcome. In addition, the sorbents described herein treat gaseous effluents sufficiently efficiently to obviate the need for secondary treatment of non-gaseous effluents produced as by-products of the primary gaseous effluent treatment process. gain the ability. The sorbents disclosed herein are also beneficial in that they are reusable. Through reprocessing methods, it is possible to collect (i.e., remove) from the sorbent hazardous contaminants that chemically bond with the amalgam-forming metals in the sorbent, thereby removing contaminants from gaseous and non-gaseous effluents. Restores the ability of the adsorbent to remove.

Further areas of applicability will become apparent from the description provided herein. The descriptions and specific examples in this summary are for illustrative purposes only and are not intended to limit the scope of the disclosure.

In another aspect of the present disclosure, an emissions control system includes a mass of reactive adsorbent comprising at least a copper-zinc-tin-sulfide (CZTS) compound within a fluidized bed apparatus. Exemplary emission control systems may further comprise one or more pre-filters and/or post-filters including reactive adsorbent masses comprising at least a CZTS compound. Depending on the requirements of a particular application, prefilters and postfilters may be arranged in parallel or in series with the fluidized bed apparatus.

According to another aspect of the present disclosure, the filtration process in the emission control systems described herein includes adding specific additives to the CZTS compounds to target specific contaminants present in the emissions. is strengthened by widening the selection of CZTS alloys.

Emission pollutants from industrial use are: Hg (mercury), As (arsenic), Ba (barium), Cd (cadmium), Cr (chromium), Cu (copper), Pb (lead), Sn (tin), P (phosphorus), NO2 (nitrogen dioxide) , NO3 (nitrate), NH3 (ammonia).

This wide variety of contaminants eliminates the potential for universal emission control strategies. Further, for example, an emission control strategy that may be effective for one pollutant in gaseous emissions may not be effective for the same pollutants in non-gaseous emissions, and vice versa.

Any international, federal, state, or local standard/regulation regarding the percentage of permissible parts per million (PPM) per pollutant in gaseous and/or non-gaseous emissions It sets different standards. Many of these standards and regulations establish different acceptable levels for pollutants depending on whether the pollutant is in gaseous emissions versus non-gaseous emissions.

The types and levels of contaminants in the effluent may be determined by sampling polluted test effluents and/or using continuous in-line monitoring equipment. Based on the test results, a particular pre-filter and/or post-filter through which the contaminated effluent is passed can be selected. The pre-filter and/or post-filter each contain masses of specific reactive sorbent compounds comprising CZTS alloyed as a broad-spectrum treatment option for specific contaminants present in the effluent. .

The types and/or levels of contaminants present in the effluent change and/or fluctuate as the effluent is discharged. Frequent and/or continuous in-line monitoring of contaminants allows the selection of specific prefilters and/or postfilters to be adjusted to specific contaminants in the effluent at any point in the effluent stream. It is possible to optimize

The present disclosure provides broad spectrum matrices that match specific types of contaminants in gaseous and non-gaseous effluents to specific reactive adsorbents that are effective in capturing and removing the corresponding contaminants. This matrix also determines the ability of a particular reactive sorbent to separate from a particular captured contaminant so that the contaminant can be recycled or disposed of, and whether the sorbent can be activated and reused in an emissions control system. adapt the

In addition to being a permanent, purpose-built system, the system can also be configured as a portable system. Examples of portable systems include, but are not limited to, truck-mounted systems, barge-mounted systems, trailer-mounted systems, and railcar-mounted systems. For portable system applications, in providing a bypass to a field-assembled system by providing a temporary emissions bypass for servicing, servicing, and/or repairing a permanently installed field-assembled system. Useful. Portable systems are also useful in implementing excess filtering capabilities in permanent, field-assembled installations while the flow rate of contaminated effluent exceeds the capacity of permanent, field-assembled systems.

There are numerous advantages of using the specialized adsorbents described herein with the disclosed apparatus and methods. In general, the ability of the effluent system disclosed by this sorbent to capture, contain and/or recycle mercury and other hazardous materials is previously not possible using known effluent control systems and methods. Another important advantage of the sorbents disclosed herein is that the sorbents can be used to treat both gaseous and non-gaseous effluents, thereby Many of the problems of known methods of treating polluted non-gaseous emissions, such as secondary emissions resulting from primary emission control treatments used, can be overcome. In addition, the sorbents described herein treat gaseous effluents sufficiently efficiently to obviate the need for secondary treatment of non-gaseous effluents produced as by-products of the primary gaseous effluent treatment process. gain the ability. The sorbents disclosed herein are also beneficial in that they are reusable. Through reprocessing methods, it is possible to collect (i.e., remove) from the sorbent hazardous contaminants that chemically bond with the amalgam-forming metals in the sorbent, thereby removing contamination from gaseous and/or non-gaseous effluents. Restores the sorbent's ability to remove material.

The drawings described herein are merely for the purpose of illustrating selected embodiments rather than all possible implementations, and are not intended to limit the scope of the disclosure.

Other advantages of the present invention will be readily appreciated by reference to the following detailed description in conjunction with the accompanying drawings. These drawings show:
1 is a schematic diagram showing a known configuration of a coal-fired power plant; FIG. 2 is a schematic diagram illustrating a known configuration of an emissions control system used to remove pollutants from emissions produced by a coal-fired power plant of the type shown in FIG. 1; FIG. 3 is a schematic diagram of the emissions control system shown in FIG. 2 and modified by adding an exemplary reverse venturi device constructed in accordance with the present disclosure; FIG. 1 is a side cross-sectional view of an exemplary reverse venturi device having a housing with an inlet, an enlarged diameter portion, and an outlet, constructed in accordance with the present disclosure; FIG. 4B is a front cross-sectional view of the inlet portion of the housing of the exemplary reverse venturi device shown in FIG. 4A; FIG. 4B is a cross-sectional front view of the enlarged diameter portion of the housing of the exemplary inverted venturi device shown in FIG. 4A; FIG. FIG. 4B is a front cross-sectional view of the outlet portion of the housing of the exemplary reverse venturi device shown in FIG. 4A; FIG. 4 is a cross-sectional side view of another exemplary reverse venturi device having a series of alternating baffles disposed in the enlarged diameter portion of the housing to form a tortuous flow path for the exhaust, constructed in accordance with the present disclosure; FIG. 4 is a side cross-sectional view of another exemplary reverse venturi device constructed in accordance with the present disclosure and having a helical baffle disposed in the enlarged diameter portion of the housing to form a helical flow path for the exhaust. 6B is a front perspective view of the helical baffle of the exemplary inverted venturi device shown in FIG. 6A; FIG. FIG. 4 is a side cross-sectional view of another exemplary inverted venturi device having a plurality of spaced apart baffles disposed in the enlarged diameter portion of the housing, constructed in accordance with the present disclosure; FIG. 7B is a front cross-sectional view of the exemplary inverted venturi device shown in FIG. 7A taken along line AA, showing one orifice of the baffle; FIG. 4 is a side cross-sectional view of another exemplary inverted venturi device having a plurality of fragments disposed in the enlarged diameter portion of the housing, constructed in accordance with the present disclosure; FIG. 4 is a side cross-sectional view of another exemplary inverted Venturi device having a plurality of entangled threads disposed in the enlarged diameter portion of the housing to form a filament, constructed in accordance with the present disclosure; FIG. 4 is a side cross-sectional view of another exemplary inverted venturi device having a filter element disposed in the enlarged diameter portion of the housing, constructed in accordance with the present disclosure; FIG. 4 is a cross-sectional side view of another exemplary inverted venturi device constructed in accordance with the present disclosure, in which the enlarged diameter portion of the housing accommodates a plurality of baffles and a plurality of various sized debris disposed between adjacent baffles; FIG. 12 is a front view showing an example of a fragment sized to be accommodated in the enlarged diameter portion of the housing of the exemplary inverted venturi device shown in FIG. 11; FIG. 12 is a front view of another example of debris sized to be accommodated in the enlarged diameter portion of the housing of the exemplary inverted venturi device shown in FIG. 11; FIG. 12 is a front view of another example of debris sized to be accommodated in the enlarged diameter portion of the housing of the exemplary inverted venturi device shown in FIG. 11; FIG. 12 is a front view of another example of debris sized to be accommodated in the enlarged diameter portion of the housing of the exemplary inverted venturi device shown in FIG. 11; FIG. 12 is a front view of an example of an asterisk-shaped piece of loose material that can be used in combination with other pieces to replace the debris shown in the exemplary inverted venturi device of FIGS. 8 and 11; FIG. 12 is a front view of an example of a crystalline flake that can be used in combination with other crystalline flakes to replace the fragments shown in the exemplary inverted venturi device of FIGS. 8 and 11; FIG. 12 is a front view of one example of a wire coil that can be used in combination with other wire coils to replace the debris shown in the exemplary reverse venturi device of FIGS. 8 and 11; FIG. 4 is a cross-sectional side view of another exemplary inverted venturi device having two separate flared portions connected in series and constructed in accordance with the present disclosure; FIG. 4 is a cross-sectional side view of another exemplary inverted venturi device having two parallel-connected, separated flared portions constructed in accordance with the present disclosure; FIG. 4 is a side cross-sectional view of another exemplary reverse venturi device constructed in accordance with the present disclosure; 1 is a block flow diagram illustrating known methods for removing contaminants from gaseous emissions; A method for removing contaminants from a gaseous effluent as shown in Figure 17, with the additional step of injecting the gaseous effluent with a sorbent at the first point of introduction and then passing the gaseous effluent through a reverse venturi device. Block diagram showing a modified method. A method for removing contaminants from a gaseous effluent as shown in Figure 17 with the additional step of injecting the gaseous effluent with a sorbent at a second point of introduction and thereafter passing the gaseous effluent through a reverse venturi device. Block diagram showing a modified method. 1 is a block diagram illustrating a known method of removing contaminants from non-gaseous effluent, which method requires settling the non-gaseous effluent in a sedimentation basin; FIG. Block showing the method of removing contaminants from the non-gaseous effluent shown in Figure 19, modified to add the step of treating a portion of the sorbent-extracted non-gaseous effluent from the sedimentation basin. figure. 4 is a graph showing the percentage of contaminants removed from effluents by known emissions control systems and the percentage of contaminants removed from effluents by the apparatus and methods disclosed herein. 1 is a block flow diagram illustrating an example of the use of an inverted venturi fluidized bed device to remove contaminants from a gaseous effluent and to wash reactants to separate the contaminants from the gaseous effluent. 1 is a block flow diagram illustrating an example of the use of an inverted venturi fluidized bed device to remove contaminants from non-gaseous effluent and to wash reactants to separate contaminants from non-gaseous effluent. 1 is a flow diagram showing extended non-turbulent effluent flow through an exemplary inverted venturi fluidized bed apparatus and exemplary method steps for washing and recycling adsorbents that separate contaminants from the effluent. 1 is a block flow diagram illustrating an example of a method using an inverted venturi fluidized bed apparatus with a tilting mechanism mounted on a portable pedestal deck, wherein the housing of the inverted venturi fluidized bed apparatus is the gaseous effluent; oriented parallel to the gantry deck to remove contaminants from the FIG. 3 is a side view of an inverted venturi fluid bed apparatus of the present disclosure, with the tilt mechanism mounted to the portable cradle deck and the housing of the inverted venturi fluid bed apparatus oriented parallel to the cradle deck; 1 is a block flow diagram showing an example of a method using an inverted venturi fluidized bed apparatus with a tilting mechanism mounted on a portable pedestal deck, wherein the enclosure of the inverted venturi fluidized bed apparatus is non-gas exhaust; It is oriented transversely to the gantry deck to remove contaminants from the object. FIG. 3 is a side view of an inverted venturi fluid bed apparatus of the present disclosure with the tilt mechanism mounted to the portable cradle deck and the enclosure of the inverted venturi fluid bed apparatus oriented transversely to the cradle deck; FIG. 4 is a side view of an inverted venturi fluid bed apparatus of the present disclosure with the tilt mechanism mounted to the portable cradle deck and the housing of the inverted venturi fluid bed apparatus oriented at approximately 45 degrees to the cradle deck; FIG. 30 is a side view of an inverted venturi fluidized bed apparatus of the present disclosure with a tilting mechanism mounted on the portable cradle deck shown in FIGS. 26, 28 and 29 showing the total sweep angle of the tilting mechanism; FIG. 2 is a rear view of an inverted venturi fluid bed apparatus of the present disclosure with a tilting mechanism mounted on a portable pedestal deck rotating clockwise or counterclockwise while reciprocating the housing of the inverted venturi fluid bed apparatus; shows how to rotate to 1 is a rear view of an inverted venturi fluid bed apparatus of the present disclosure with a tilting mechanism mounted on a portable cradle deck, wherein the housing of the inverted venturi fluid bed apparatus is transverse to the cradle deck; FIG. Oriented. Matrix showing specific contaminant types that match the effectiveness of the disclosed CZTS alloy adsorbents as compared to activated carbon and zeolite adsorbents for gaseous and non-gaseous emissions. Schematic diagram showing certain CZTS alloy sorbents compared to other specific contaminant types for gaseous and non-gaseous emissions. A matrix demonstrating existing sorbents and their ability to separate and recycle contaminants in gaseous and non-gaseous effluents. A matrix demonstrating the disclosed broad-spectrum CZTS alloy sorbents and their ability to separate and recycle contaminants in gaseous and non-gaseous effluents. FIG. 4 is a block diagram showing how a contaminated gaseous effluent is passed through different filters containing specific effective adsorbents that match the type and/or level of contaminants in the gaseous effluent. FIG. 4 is a block diagram showing how a contaminated non-gaseous effluent is passed through different filters containing specific effective adsorbents that match the type and/or level of contaminants in the non-gaseous effluent.

An apparatus and method for removing pollutants from industrial effluents will be described with reference to the drawings, wherein like numerals indicate corresponding elements throughout.

Exemplary embodiments are described more fully with reference to the accompanying drawings. These exemplary embodiments are provided so that this disclosure will be thorough and complete, and will fully convey the scope to those skilled in the art. Numerous specific details are set forth, including examples of specific components, devices and methods, in order to provide a thorough understanding of the disclosed embodiments. It will be apparent to those skilled in the art that the specific details need not be used and that the example embodiments can be implemented in many different forms and should not be construed as limiting the present disclosure. In some exemplary embodiments, well-known methods, well-known device structures, and well-known techniques are not described in detail.

The terminology used herein is for the purpose of describing particular example embodiments only and is not intended to be limiting. As used herein, the singular is intended to include the plural unless explicitly stated otherwise. The terms "comprising", "comprising", "including" and "having" are inclusive and specify the presence of the stated features, integers, steps, acts, elements and/or parts. However, it does not exclude the presence or addition of one or more features, integers, steps, operations, elements, parts and/or groups. Method steps, processes and operations described herein should not be construed as requiring performance in the particular order described or illustrated, unless specifically specified as an order of performance. Of course, additional or alternative steps may be used.

When an element or layer is referred to as being “on”, “engaging with,” “connected to,” or “coupled to” another element or layer, that element or layer is directly on the other element or layer. may be in, engage, connect or couple. Alternatively, there may be intervening elements or layers. On the other hand, when an element is referred to as being "directly on," "directly engaging with," "directly connected to," or "directly connected to," another element or layer, there are no intervening elements or layers. you can Other terms used to describe relationships between elements (e.g., "between" and "directly between," "adjacent" and "directly adjacent," etc.) should be construed in the same manner. It should be. As used herein, the term "and/or" includes all combinations of one or more associated list items.

Although the terms first, second, third, etc. are used herein to describe various elements, components, regions, layers and/or cross-sections, these elements, components, regions, layers and/or Or the cutting plane is not limited by these terms. These terms may only be used to distinguish one element, component, region, layer and/or section from another region, layer or section. Terms such as "first," "second," and other numerical terms when used herein do not imply an arrangement or order, unless the context clearly indicates. Thus, first elements, components, regions, layers and/or cut surfaces discussed below may be referred to as second elements, components, regions, layers and/or cut surfaces without departing from the teachings of the examples. is also possible.

Spatially relative terms such as "inner", "outer", "beneath", "beneath", "below", "above", "above", etc. are used in the illustrations. May be used herein to facilitate describing the relationship of an element or feature to other elements or features. Spatially relative terms may encompass different orientations of the device in use or operation in addition to the orientation shown. For example, when the device in the figures is turned over, an element described as "below" or "beneath" another element or feature would be placed "above" the other element or feature. Thus, the exemplary term "below" can encompass both up and down orientations. The device may be oriented in other directions (rotated 90 degrees or in other orientations) and the spatially related descriptions used herein should be construed accordingly.

In addition, the term "conduit" as used herein covers the description of all pipes normally available for carrying liquids and/or liquid effluents and gases and/or gaseous effluents. is intended to be No preference is given or implied as to the actual method of transporting any Emission regardless of the type of Emission.

Referring to FIG. 1, a schematic diagram of a typical coal-fired power plant 100 is shown. This coal-fired power plant 100 has a fluidized bed reactor 1 which is an industrial installation that burns one or more coal fuels 2 to generate electricity 7 . This power 7 may then be distributed to the grid via wires 8 . Combustion in the fluidized bed reactor 1 is carried out by air 3 , fire 4 and coal fuel 2 . This combustion process is used to heat water and generate steam 5 . This steam is then used to turn a generator 6 to generate electricity 7 . Gaseous emissions 10 from the combustion process are discharged into the environment through a chimney 9 . If no emissions control system were installed in the coal-fired power plant 100 (FIG. 1), the emissions 10 would be fly ash, mercury (Hg), metal vapors, sulfur dioxide (SO2), hydrogen chloride (HCl) and Contains many harmful pollutants such as other noxious gases.

Referring to FIG. 2, a schematic diagram of a modified coal-fired power plant 200 having a conventional emissions control system 202 is shown. The emissions control system 202 traps and collects a portion of the hazardous pollutants in the gaseous emissions 10 . This effluent control system 202 includes a wet/dry scrubber 11 that removes some of the sulfur dioxide and fly ash contaminants from the gaseous effluent 10 from the fluidized bed reactor 1 in which the combustion reaction takes place. transport to Alternatively, or in addition to conveying the gaseous effluent 10 to the wet/dry scrubber 11, the emissions control system 202 may remove the gaseous effluent 10 from sulfur dioxide, noxious gases and one of other pollutants. It may be conveyed to a jet dryer 12 where the parts are caught and collected. This effluent may be passed through a textile filter unit 13 (or baghouse) that removes particles from the stream of gaseous effluent 10 using filter bags. This system collects and removes many pollutants from the gaseous effluent 10 before it is discharged through the chimney 9 into the surrounding atmosphere (ie, the environment). A problem with the conventional emission control system 202 shown in FIG. machine 12 and fiber filter unit 13.

Referring to FIG. 3, there is shown a schematic diagram of a modified coal-fired power plant 300 having an sorbent injector 14 and a reverse venturi device 15 in addition to the emissions control system 202 shown in FIG. The sorbent injector 14 operates to add sorbent to the gaseous effluent 10 and may be positioned upstream of the reverse venturi device 15 . More specifically, in the example shown in FIG. 3, the sorbent injector is positioned between the jet dryer 12 and the fiber filter unit 13 . In FIG. 3 the reverse venturi device 15 is positioned between the fiber filter unit 13 and the chimney 9, although different positions of the reverse venturi device 15 are possible. One of the major advantages of this arrangement is that the reverse venturi device 15 can be installed in existing installations, requiring only a "Modification to Existing Permit" to be applied, and a completely new emission control system. It saves both time and money compared to applying for a system. In operation, gaseous effluent 10 is directed from fiber filter unit 13 to reverse venturi device 15 . As will be described in more detail below, this reverse venturi device 15 is provided with internal structures suitable for collecting and trapping substantial quantities of mercury, heavy metals, nano-sized particles and other contaminants. The gaseous effluent 10 exiting the chimney 9 is therefore substantially free of all harmful pollutants.

As shown in Figures 4A-4D, the inverted venturi device 15 has a housing 16 that is in the shape of an inverted venturi. Of course, a venturi is generally described as a conduit that first contracts from a larger cross-section to a smaller cross-section and then expands from the smaller cross-section to a larger cross-section. Accordingly, the term "inverted venturi" as used herein means the opposite, i.e., a conduit that first expands from a smaller cross-section to a larger cross-section and then contracts from the larger cross-section to a smaller cross-section. . Specifically, the housing 16 of the disclosed inverted venturi device 15 extends along a central axis 17 and has an inlet section 18 , an enlarged diameter section 19 and an outlet section 20 . The inlet portion 18 of this enclosure 16 is sized such that the gaseous effluent 10 enters at a predetermined inlet flow velocity characterized by an inflow velocity V1 and a pressure P1. The outlet section 20 of this enclosure 16 is sized such that the gaseous effluent 10 exits at a predetermined outlet flow rate characterized by an outlet velocity V3 and a pressure P3. This enlarged diameter portion 19 is located between the inlet portion 18 and the outlet portion 20 of the housing 16 and forms an enlarged diameter chamber 21 therein for trapping contaminants in the gaseous exhaust 10 . The enlarged diameter portion 19 of the housing 16 has an inner surface 68 approximately facing the central axis 17 . The inlet portion 18, the enlarged diameter portion 19, and the outlet portion 20 of the housing 16 are in fluid communication with each other along the central axis 17. are arranged in order to That is, inlet portion 18 , enlarged diameter portion 19 , and outlet portion 20 of housing 16 together form a conduit extending along central axis 17 .

Inlet 18 of housing 16 has an inlet cross-sectional area A 1 transverse to central axis 17 and outlet 20 of housing 16 has an outlet cross-sectional area A 3 transverse to central axis 17 . The inlet cross-sectional area A1 may be equal (ie, identical) to the outlet cross-sectional area A3 such that the predetermined inlet flow rate is equal (ie, identical) to the predetermined outlet flow rate. Alternatively, the inlet cross-sectional area A1 and the outlet cross-sectional area A3 are different (i.e., smaller or larger) such that the predetermined inlet flow rate is different (i.e., smaller or larger) than the predetermined outlet flow rate. ) is also good. As used herein, the term "flow rate" refers to the volumetric flow rate of the effluent.

Enlarged diameter portion 19 of housing 16 traverses central axis 17 and has an enlarged diameter cross-sectional area A2 that is greater than inlet cross-sectional area A1 and outlet cross-sectional area A3. Therefore, the enlarged diameter portion 19 is such that the flow velocity V2 of the exhaust gas 10 in the enlarged diameter portion 19 of the housing 16 is smaller than the flow velocity V1 of the exhaust gas 10 in the inlet portion 18 of the housing 16, and It is sized to be less than the flow velocity V3 of the gaseous effluent 10 in the outlet 20 of the body 16 . Such a decrease in flow velocity increases the residence time of the exhaust gas 10 within the enlarged diameter portion 19 of the housing 16 . As used herein, the term "residence time" refers to the average amount of time required for molecules within gaseous exhaust 10 to pass through enlarged diameter portion 19 of housing 16. FIG. That is, the "residence time" of the enlarged diameter portion 19 of the housing 16 is equal to the time required for all the discharges in the enlarged diameter chamber 21 to be renewed. Also, as used herein, the term "cross-sectional area" refers to an internal cross-sectional area (ie, the space inside housing 16) that is the same regardless of changes in housing 16 thickness. Accordingly, the expanded diameter section cross-sectional area A2 reflects the size of the expanded diameter chamber 21 and is defined by the inner surface 68 .

Due to the shape of the housing 16, the internal pressure P1 of the gaseous emissions 10 passing through the inlet 18 of the housing 16 and the internal pressure P3 of the gaseous emissions 10 passing through the outlet 20 of the housing 16 are It is greater than the internal pressure P2 of the gas discharge 10 passing through the enlarged diameter portion 19 . The flow velocity V2 of the gas emission 10 in the enlarged diameter portion 19 of the housing 16 is smaller than the flow velocity V1 of the gas emission 10 at the inlet 18 of the housing 16, and the gas discharge at the outlet 20 of the housing 16. This pressure differential, combined with the fact that the flow velocity of the material 10 is less than V3, causes the gaseous exhaust material 10 to accumulate in the enlarged diameter portion 19 of the housing 16 . As a result of the pressure and velocity differentials described above, and because the gas discharge 10 will naturally expand to occupy the entire volume of the expanded diameter chamber 21, the gas discharge 10 within the enlarged diameter portion 19 of the housing 16 will will be subjected to an expansion force. This fact, combined with effects due to laminar flow, pneumatic dynamics, and gas behavior physics, effectively removes Increased ability to capture and thereby remove contaminants.

Housing 16 may be of a variety of different shapes and configurations. As a non-limiting example, inlet portion 18, enlarged diameter portion 19, and outlet portion 20 of housing 16 shown in FIGS. 4A-4D all have circular cross-sectional areas A1, A2, A3. Alternatively, the cross-sectional areas A1, A2, A3 of one or more of the inlet portion 18, the enlarged diameter portion 19 and the outlet portion 20 of the housing 16 may be non-circular, and may be of circular and non-circular cross-sections. Various combinations are possible and are considered within the scope of this disclosure. In some constructions, the enlarged diameter portion 19 of the housing 16 may have a diverging end 22 and a converging end 23 . According to these structures, the enlarged diameter portion 19 of the housing 16 tapers outward from the inlet cross-sectional area A1 to the enlarged diameter cross-sectional area A2 at the divergent end 22 . That is, the cross-section of the enlarged diameter portion 19 of the housing 16 increases at the divergent end 22 as it moves away from the inlet 18 of the housing 16 . On the other hand, the enlarged diameter portion 19 of the housing 16 tapers gradually inward at the converging end 23 from the enlarged diameter portion cross-sectional area A2 to the outlet cross-sectional area A3. That is, the cross section of the enlarged diameter portion 19 of the housing 16 becomes smaller at the converging end 23 as it moves in the direction toward the exit portion 20 of the housing 16 . Accordingly, the gaseous emissions 10 within the enlarged diameter portion 19 of the housing 16 flow approximately from the diverging end 22 to the converging end 23 . In embodiments in which the inlet portion 18, the enlarged diameter portion 19, and the outlet portion 20 of the housing 16 all have circular cross-sectional areas A1, A2, A3, the diverging and converging ends 22, 23 of the housing 16 are approximately It may be conical. Notwithstanding the above, the diverging and converging ends 22, 23 of the enlarged diameter portion 19 of the housing 16 may be differently shaped. As a non-limiting example, the diverging and converging ends 22, 23 are designed to be more manufacturable while not significantly adversely affecting the flow of the gaseous effluent 10 through the housing 16 of the reverse venturi device 15. , may be polygonal. In another alternative configuration, the enlarged diameter portion 19 of the housing 16 resembles a sausage with relatively abrupt transitions between the inlet portion 18 and the diverging end portion 22 and between the converging end portion 23 and the outlet portion 20 . It may have a shape. It is presumed that smooth transitions are preferred over abrupt transitions because the laminar flow behavior of the gaseous exhaust 10 is more favorable. However, minor disturbances to the laminar flow of the gaseous discharge 10 during abrupt changes are not considered to be an absolute problem, but rather can result in better flow in areas where increased residence time is not required. There is also sex.

With continued reference to FIGS. 4A-4D and further to FIGS. 5-11, reactant mass 24 is positioned within enlarged diameter portion 19 of housing 16 . This reactant mass 24 has a reactive outer surface 25 that is placed in contact with the gaseous effluent 10 . Additionally, this reactant mass 24 chemically bonds with at least a portion of the contaminants in the gaseous effluent 10 that pass through the enlarged diameter portion 19 of the housing 16 to reach the reacting outer surface 25 of the reactant mass 24 . It contains an amalgam-forming metal on its reactive outer surface 25 . In this way, contaminants bound to the outer reaction surface 25 of the reactant mass 24 remain trapped within the enlarged diameter portion 19 of the housing 16 and thus flow out of the enlarged diameter portion 19 of the housing 16. are removed from the stream of gaseous effluent 10 entering the outlet 20 of the housing 16 . As used herein, the term “amalgam-forming metal” means a material selected from the group of metals capable of forming compounds with one or more of the contaminants in the gaseous effluent 10 . By way of non-limiting example, the amalgam-forming metal may be zinc and the contaminant in the gaseous effluent 10 may be mercury, whereby the gaseous effluent 10 contacts the reaction outer surface 25 of the reactant mass 24. In some cases, an amalgam of zinc and mercury may be formed.

The enlarged diameter portion 19 of the housing 16 allows a predetermined inlet flow rate while ensuring a sufficiently long residence time for the amalgam-forming metals in the reactant mass 24 to chemically bond with the contaminants in the gaseous effluent 10. of gaseous effluent 10. Therefore, to achieve this balance, the expanded cross-sectional area A2 may range from 3 square feet to 330 square feet to achieve residence times ranging from 1 second to 2.5 seconds. This particular residence time is necessary to allow sufficient time for the contaminants in the gaseous effluent 10 to chemically bond with the amalgam-forming metals in the reactant mass 24 . Thus, a range of enlarged section cross-sectional areas A2 has been calculated to achieve this residence time in coal-fired power plants 100 with outputs ranging from 1 megawatt (MW) to 6000 megawatts (MW). As known in the chemical arts, the amalgam-forming metal can be a variety of different metals. As a non-limiting example, the amalgam-forming metal may be selected from the group consisting of zinc, iron and aluminum. Housing 16 is made of a different material than reactant mass 24 . As non-limiting examples, housing 16 may be made of steel, plastic or fiberglass.

Reactant mass 24 may have a variety of different and optional configurations. In FIG. 4A, reactant mass 24 is shown as coating inner surface 68 of housing 16 . Alternatively, as shown in FIGS. 5-11, the reactant mass 24 may form one or more obstruction elements 26a-26j disposed within the enlarged diameter portion 19 of the housing 16. FIG. These obstruction elements 26 a - 26 j as such form a tortuous flow path 27 for the gas exhaust 10 passing through the enlarged diameter portion 19 of the housing 16 . Obstruction elements 26 a - 26 j thus increase the residence time of gaseous emissions 10 passing through enlarged diameter portion 19 of housing 16 . In some of the embodiments described below, the tortuous flow path 27 formed is completely random because it completely disrupts the flow of the gaseous exhaust 10 through the enlarged diameter portion 19 of the housing 16. This greatly increases the chances of chemical reactions between the contaminants in the gaseous effluent 10 and the amalgam-forming metals in the reactant mass 24 .

Each obstruction element 26a-26j of the structures shown in FIGS. 5-11 has a large surface area, which increases the reactive outer surface 25 of the reactant mass 24. FIG. It collects and traps contaminants in the enlarged diameter portion 19 of the housing 16 by chemical reaction between the amalgam-forming metals in the reactive outer surface 25 of the reactant mass 24 and the contaminants in the gaseous effluent 10 . Advantageously, and/or collectible, contaminants are removed from the gaseous effluent 10 . Therefore, the amount of contaminants that can be removed from the gaseous effluent 10 passing through the diametrically enlarged chamber 21 by the diametrically enlarged portion 19 of the housing 16 is determined by proportional to the size of 25. In addition, the complex surface geometry and/or texture of the obstruction elements 26a-26j may prevent contaminant entrapment, whether or not contaminant entrapment is the result of a chemical reaction between the contaminant and the amalgam-forming metal. Additional surface area is provided to facilitate physical trapping.

Referring again to FIG. 3, the sorbent added to the effluent by sorbent injector 14 includes amalgam-forming metals. The amalgam-forming metals in the adsorbent chemically bond with at least some contaminants in the gaseous effluent 10 before the gaseous effluent 10 enters the enlarged diameter portion 19 of the housing 16 . The adsorbent may be, for example, zinc (Zn) powder or a copper-zinc-tin-sulfide (CZTS) compound, although the adsorbent may have many different compositions. Because the sorbent chemically bonds with at least some of the contaminants in the gaseous effluent 10 before the gaseous effluent 10 enters the enlarged diameter portion 19 of the housing 16, the sorbent causes the reactant mass to Removal of contaminants from the gaseous effluent 10 by 24 is facilitated.

As shown in FIG. 5, obstruction elements 26 a - 26 j are provided as a series of interleaved baffles 26 a extending from inner surface 68 of enlarged diameter portion 19 of housing 16 . This series of interleaved baffles 26a traverses the central axis 17 and gives the tortuous channel 27 a serpentine shape. The serpentine shape of this tortuous channel 27 increases the residence time of the gaseous effluent 10 within the enlarged diameter portion 19 of the housing 16, thereby causing the gaseous discharge by the reactant masses 24 forming a series of interleaved baffles 26a. The capture and removal of contaminants in article 10 is facilitated. In one example, this series of alternating baffles 26a is made of zinc. In another example, the series of alternating baffles 26a are of a material other than zinc coated with zinc. The arrangement of interleaved baffles 26a need not be evenly spaced or symmetrical along the length of central axis 17; This is because in some applications a wider space between adjacent baffles 26a is preferred and in other applications a narrower space between adjacent baffles 26a is preferred. Also, this series of interleaved baffles 26a may be replaced and/or cleaned as needed if they become saturated during operation of the reverse venturi device 15 .

As shown in FIGS. 6A-6B, at least one obstruction element 26a-26j may be a helical baffle 26b. The helical baffle 26 b extends along the central axis 17 and spirally within the enlarged diameter portion 19 of the housing 16 with the central axis 17 as the center. Therefore, the spiral baffle 26b gives the curved flow path 27 a spiral shape. The helical shape of this tortuous flow path 27 increases the residence time of the gaseous effluent 10 within the enlarged diameter portion 19 of the housing 16, thereby increasing the gaseous effluent 10 by the reactant mass 24 forming the helical baffle 26b. The capture and removal of contaminants within is facilitated. In one example, this spiral baffle 26b is made of zinc. In another example, the helical baffle 26b is made of a material other than zinc coated with zinc. In yet another example, the helical baffle 26b is mechanically driven to rotate within the enlarged diameter portion 19 of the housing 16 about the central axis 17. As shown in FIG. By rotating the spiral baffle 26b, the flow of the gaseous exhaust 10 through the enlarged diameter portion 19 of the housing 16 can be artificially accelerated or decelerated depending on the direction of rotation of the spiral baffle. This helical baffle 26b may be replaced and/or cleaned as necessary if it becomes saturated during operation of the reverse venturi device 15 .

As shown in FIGS. 7A-7B, at least one obstruction element 26a-26j is a plurality of baffles 26c. Each baffle 26 c extends from the inner surface 68 of the enlarged diameter portion 19 of the housing 16 across the enlarged diameter portion 19 of the housing 16 . The baffles 26c are spaced apart along the central axis 17 and each baffle 26c has an orifice 28 that permits the flow of gaseous exhaust 10 past the baffle 26c. Of course, any number of baffles 26c may be provided, including configurations having only a single baffle 26c. The size, shape and number of orifices 28 in each baffle 26c can vary. For example, baffle 26c may be screen-like and orifice 28 may be provided between the crosshairs of the screen. The orifice 28 in this baffle 26c restricts the flow of the gaseous effluent 10 within the enlarged diameter portion 19 of the housing 16 and increases the residence time of the gaseous effluent 10 within the enlarged diameter portion 19 of the housing 16. FIG. This facilitates the capture and removal of contaminants from gaseous exhaust 10 by reactant mass 24 forming baffle 26c. In one example, this baffle 26c is made of zinc. In another example, this baffle 26c consists of a material other than zinc coated with zinc. This baffle 26c may be replaced and/or cleaned as necessary if it becomes saturated during operation of the reverse venturi device 15. FIG. In yet another example, the orifice 28 size of one baffle 26c differs from the orifice 28 size of an adjacent baffle 26c. The use of different sized orifices 28 in different baffles 26c accelerates and/or restricts the flow of gaseous effluent 10, allowing the trapping and removal of contaminants in gaseous effluent 10 by reactant masses within baffles 26c. can be promoted. Similarly, the baffles 26c need not be evenly spaced in the expanded chamber 21, and the orifices 28 of one baffle 26c need not be the same size, shape or location as the orifices 28 of adjacent baffles 26c. good. By varying the size, shape and location of these orifices 28 from one baffle 26c to another baffle 26c, and by varying the spacing of the baffles 26c, residence time of gaseous effluent 10 can be increased to facilitate increased contact with physical and chemical trapping and collection points along reactant mass 24 .

In another configuration shown in FIGS. 8-11, at least one obstruction element 26a-26j may not be fixed to housing 16 itself, but instead be free to extend within enlarged diameter portion 19 of housing 16. may be placed. In such configurations, at least one obstruction element 26a-26j may include various forms of obstruction media 26d-26j. Like the obstruction elements 26a-26c, the obstruction media 26d-26j may be of zinc or of a material other than zinc that is coated with zinc. Zinc is readily soluble and can be cast into complex shapes using conventional molding methods, loss wax methods, centrifugation methods, and the like. Other forming methods include cutting, extrusion, sintering, stamping, hot forging and forming, laser cutting, and the like. Alternatively, steel may be used for prototyping and then coated or plated with zinc as a surface cover. This obstruction medium 26d-26j can be used to completely fill the entire expanded chamber 21, partially fill the expanded chamber 21, or fill between the baffles 26c previously described in connection with FIGS. 7A-7B. It is possible.

FIG. 8 shows an arrangement in which at least one obstruction element 26a-26j is a plurality of fragments 26d housed within the enlarged diameter portion 19 of the housing 16. FIG. According to this configuration, the gaseous emissions 10 are separated from the adjacent fragments 26d as the gaseous emissions 10 move through the enlarged diameter portion 19 of the housing 16 from the inlet portion 18 of the housing 16 toward the outlet portion 20. pass through the space between For this reason, the plurality of fragments 26 d may be irregular in shape so that the fragments 26 d are loosely packed within the enlarged diameter portion 19 of the housing 16 . As a non-limiting example, the plurality of pieces 26d may consist of mossy zinc. Modi zinc is a popcorn-shaped zinc structure that is produced by immersing molten zinc in a cooling liquid such as water. The resulting droplets of molten zinc solidify into relatively small, spherical structures with a very high surface area to volume ratio. Additionally, the surface area of the resulting structure has a mossy surface texture. These structures can be sized for specific applications. By working steel, it is possible to produce composite spherical structures of steel plates similar to modzii zinc, which may be coated with zinc.

The loose packing of these multiple fragments 26d in FIG. 8 results in a random shape of the tortuous flow path 27, which reduces the residence time of the gaseous exhaust 10 within the enlarged diameter portion 19 of the housing 16. To increase. This facilitates the capture and removal of contaminants from the gaseous effluent 10 by the reactant mass 24 forming a plurality of fragments 26d. This plurality of debris 26d in FIG. 8 may be replaced and/or cleaned as needed if it becomes saturated during operation of the reverse venturi device 15. FIG.

In another configuration shown in FIG. 9, at least one of the obstructing elements 26a-26j is a plurality of entangled threads 26e housed within the enlarged diameter portion 19 of the housing 16. As shown in FIG. The plurality of entangled threads 26 e form a thread-like body within the enlarged diameter portion 19 of the housing 16 . In one possible configuration, the plurality of entangled threads 26e are folded and rolled like steel wool to form a clump with a very large surface area. The entangled yarns 26e themselves may be of the same composition, thickness and length, or may be a combination of different compositions, thicknesses and/or lengths. In one example, these multiple entangled yarns 26e consist of zinc wires and are randomly entangled to form zinc wool. This zinc wool can be made from wires of varying levels of density and/or size to impart specific flow restriction capabilities. In another example, these multiple entangled yarns 26e consist of steel wires that are randomly entangled to form steel wool. This steel wool may be coated with zinc. The loose packing of these multiple entangled threads 26e in FIG. time increases. This facilitates the capture and removal of contaminants within the gaseous exhaust 10 by the reactant mass 24 forming the plurality of entangled threads 26e. These multiple entangled threads 26e may be replaced and/or cleaned as needed if they become saturated during operation of the reverse venturi device 15 .

Referring to FIG. 10, another alternative arrangement is shown in which the at least one obstructing element 26a-26j is a filter element 26f. The filter element 26 f extends across the enlarged diameter portion 19 of the housing 16 with respect to the central axis 17 . The filter element 26f is porous and the pores in the filter element 26f allow the gaseous exhaust 10 to flow through the enlarged diameter portion 19 of the housing 16 from the inlet 18 to the outlet 20 of the housing 16. It is allowed to pass through the filter element 26f. This configuration of the filter element 26f, which may be of sintered metal, results in a random shape of the tortuous flow path 27, which increases the residence time of the gaseous effluent 10 passing through the enlarged diameter portion 19 of the housing 16. . This facilitates the capture and removal of contaminants in gaseous exhaust 10 by reactant mass 24 forming filter element 26f. The sintered metal of filter element 26f preferably comprises zinc or a non-zinc material coated with zinc. This filter element 26f may be replaced and/or cleaned as necessary if it becomes saturated during operation of the reverse venturi device 15. FIG.

Referring to FIG. 11, as a combination of baffles 26c shown in FIGS. 7A-7B and fragments 26g-26j of different sizes and similar to fragments 26d shown in FIG. At least one obstruction element 26a-26j is shown. According to this alternative configuration, the plurality of baffles 26c and the plurality of fragments 26g-26j are located within the enlarged diameter portion 19 of the housing 16. FIG. Similar to FIGS. 7A-7B, the plurality of baffles 26c shown in FIG. Further, the plurality of baffles 26c are spaced apart from each other along the central axis 17 such that the baffles 26c divide the expanded diameter chamber 21 into a plurality of compartments. An orifice 28 in each baffle 26c allows the flow of gaseous effluent 10 to pass through the baffle 26c. A plurality of fragments 26g-26j are positioned between adjacent baffles 26c (ie, positioned within a plurality of compartments of expanded diameter chamber 21).

A plurality of fragments 26g-26j form reactant mass 24, as shown in FIGS. 11 and 12A-12D. These plurality of pieces 26g-26j are of different sizes, grouped with pieces of the same size (i.e., pieces 26g, 26h, 26i, and 26j are grouped separately) and pieces of different sizes. may be separated by baffle 26c. For example, groups of fragments 26g-26j may be arranged such that the size of fragments 26g-26j move away from inlet 18 of housing 16 and decrease in size as they approach outlet 20 of housing 16. FIG. That is, the size of each group of fragments 26g to 26j may be gradually changed so that the gas emission 10 becomes smaller in the overall flow direction within the enlarged diameter portion 19 of the housing 16. FIG. In one example, the pieces 26g-26j are made of zinc. For example, fragments 26g-26j can be formed by dripping molten zinc into a coolant to create popcorn-shaped structures with very large surface areas and random mossy textures. In another example, pieces 26g-26j of different sizes may be mixed together and not separated based on size.

In Figures 13A-13C, several alternative forms of obstruction elements 26k-26m are shown as incompressible material, which in addition to the plurality of fragments 26d and 26g-26j shown in Figures 8 and 11, Or it can be used in place of this. FIG. 13A shows an example where an obstacle 26k forms a reactant mass 24 and has an asterisk shape resembling "Jacks" children's toys. FIG. 13B shows another form of obstructing elements 26k-26m is a plurality of crystal flakes 26l (only one shown) forming reactant mass 24 and fragments 26d and 26g-26j shown in FIGS. An example in which it may be arranged in the enlarged diameter portion 19 of the housing 16 is shown. This crystal flake 26l has a shape similar to a snowflake. FIG. 13C shows another form of obstruction elements 26k-26m is a plurality of wire coils 26m (only one shown) forming reactant mass 24 and fragments 26d and 26g-- shown in FIGS. An example in which it may be arranged in the enlarged diameter portion 19 of the housing 16 like 26j is shown. Obstacle 26k and plurality of crystal flakes 26l may be zinc or a non-zinc material coated with zinc using various processes such as, but not limited to, lost wax forging and 3D printing. may consist of The plurality of wire coils 26m are formed by, for example, winding zinc wire around a spring-like mandrel core and then cutting the entire coil of wound wire along the entire length of the mandrel core to form rings of individual coils. may be made by obtaining The different-shaped obstruction elements 26k to 26m may or may not completely fill the enlarged diameter chamber 21 .

Various combinations may be formed by mixing the various obstruction elements 26a-26k described above. An example of this mixed combination is one or more baffles 26a-26c shown in FIGS. including combining with Another mixed combination example includes combining a plurality of entangled yarns 26e shown in FIG. 9 with a plurality of pieces 26d and 26g-26j shown in FIGS. Other configurations are possible that combine the various obstruction elements 26a-26k described above with other filter elements such as activated carbon. Activated carbon, like a sponge, collects contaminants by surface contact. Accordingly, a limited amount of activated carbon may be introduced into the enlarged diameter portion 19 of the housing 16 to work with the various obstruction elements 26a-26k described above. Preferably, the obstruction elements 26 a - 26 k retain the activated carbon within the enlarged diameter portion 19 of the housing 16 such that the activated carbon is relatively statically distributed throughout the enlarged diameter chamber 21 . This configuration is contrary to conventional emission control systems that release activated carbon into the stream of gaseous emissions 10 . Activated carbon can be used more efficiently because it does not flow freely with the gaseous effluent. Those skilled in the art will appreciate that the disclosed examples of reverse venturi devices 15 are merely exemplary, and that numerous combinations beyond the few examples disclosed herein are possible and desirable to accommodate particular applications. you will easily understand.

Referring to FIG. 14, another exemplary reverse venturi device 15' comprising two enlarged diameter portions 19, 19' connected in series by a conduit 38 is shown. One enlarged diameter portion 19 of housing 16 extends between inlet portion 18 of housing 16 and conduit 38 and the other enlarged diameter portion 19 ′ extends between conduit 38 and outlet portion 20 of housing 16 . Extend. Accordingly, the tortuous path 27 of the gas discharge 10 is lengthened. With this arrangement, the gaseous effluent 10 is channeled from the enlarged diameter portion 19 through the conduit 38 to the enlarged diameter portion 19' where further contaminants are collected and/or captured. The present disclosure is not limited to using only one or two flares 19, 19' in series. This is because in some applications with large emissions and/or high levels of pollutants, it may be necessary to connect a large number of flares in series.

Referring to FIG. 15, there is shown another exemplary inverted venturi device 15'' comprising two enlarged diameter portions 19, 19'' connected in parallel. A three-way inlet valve 39 controls the flow of gaseous effluent 10 and allows gaseous effluent 10 to enter conduit 41 or conduit 42 . Three-way outlet valve 40 allows gaseous exhaust 10 to flow out of conduit 41 or conduit 42 without direct backflow from conduit 41 to conduit 42 or from conduit 42 to conduit 41 . Gas effluent 10 flows from inlet 18 into enlarged diameter 19 and out of outlet 20 as gas effluent 10 is directed through conduit 41 . Gas effluent 10 flows from inlet 18 ″ into enlarged diameter 19 ″ and out of outlet 20 ″ as gas effluent 10 is directed from conduit 42 . One of the advantages of this reverse venturi device 15'' shown in FIG. 15 is that maintenance of one of the flares 19, 19'' is not required because the other one of the flares 19, 19'' can remain operational. , if repair or cleaning is required, it can be isolated and taken offline without shutting down the entire system.

Over time, chemical reactions and/or physical entrapment of contaminants on the outer reaction surface 25 of the reactant mass 24 can cause the reactant mass 24 to reach a saturation point and reduce the efficiency of the reverse venturi device 15 . have a nature. Thus, in the configuration shown in FIG. 15, the removal, replacement and/or cleaning of the reactant mass 24 within the enlarged diameter portion 19, 19'' of the housing 16 allows the reverse venturi device to be operated without a complete shutdown. can be restored to the efficiency before saturation.

The process of removing contaminants from the saturated reactant mass depends on the specific contaminant type and the type of amalgam-forming metal used. Access to the enlarged diameter chambers 21, 21'' located inside the enlarged diameter portions 19, 19'' of the housing 16 depends on the type of obstacle used. If relatively small, incompressible obstructions are used, a pouring and/or draining type of access is required. If the obstacle is a relatively large block, plate, baffle or assembly, proper lifting and handling methods and access are required.

Still referring to FIG. 15 , the reverse venturi device 15 may have one or more spray nozzles 81 in fluid communication with the enlarged diameter portions 19 , 19 ″ of the housing 16 . The spray nozzle 81 is positioned to spray deoxygenated acid onto the reactant mass 24 within the enlarged diameter portion 19 , 19 ″ of the housing 16 . In operation, the oxygen scavenger flushes contaminants from the reactant mass 24 to rejuvenate the reactant mass 24 . Alternatively, drain 82 may be in fluid communication with enlarged diameter portions 19, 19'' of housing 16 to carry spent oxygen scavengers and contaminants out of enlarged diameter portions 19, 19'' of housing 16. can be Saturated zinc, whether coated on steel or in solid zinc structures, is preferred in that it can be recycled and reused. Therefore, the materials used in the obstacles are reusable. In addition, many of the captured contaminants, especially heavy metals such as mercury, are reusable for lighting and chlorine production.

Referring to FIG. 16, another exemplary reverse venturi device 15 is shown in which the expanded diameter chamber 45 has a significantly larger volume compared to the volumes of the inlet conduit 43 and outlet conduit 44 . The enlarged diameter portion 46 may be circular, square, triangular, elliptical, or virtually any other shape desired to provide an enlarged tortuous flow path 77 for the gaseous discharge flowing through the enlarged diameter portion 46 . It can be any one (a rectangular shape is shown).

Referring to FIG. 17, a block diagram of a typical gas emission control system is shown. Gaseous effluent is introduced from the furnace 47 into an electrostatic precipitator (ESP) 48, a fluidized gas desulfurization (FGD) unit 49, and a fiber filter (FF) unit 50 before being discharged to the atmosphere via a chimney 51. be done. A first concentration of contaminants 52 is removed from the gaseous effluent at ESP 48 . Similarly, a second concentration of contaminants 53 is removed from the gaseous effluent in the FGD unit 49 . The second concentrate 53 produced by the FGD unit 49 often contains mercury and other heavy metals and typically flows into waste water. A third concentration of contaminants 54 is removed from the gaseous effluent in the FF unit 50 .

Ultimately, final emissions to the atmosphere may still fail to meet EPA emissions rules and regulations. Acceptable EPA emissions require at least 90% of hazardous pollutants to be removed, whereas current typical emission control systems can only remove 88-90% of hazardous pollutants. . A major problem in industries producing polluting emissions is that the regulations governing emissions will become more stringent over time, while current emissions control technologies are potentially reaching their limits. That's what it means. Therefore, the pace of technological progress currently taking place has not kept up with the pace of ever more stringent emissions regulations.

18A-18B, the block diagram of FIG. 17 is modified in that a sorbent injection point is introduced and an additional step is provided in which the gaseous effluent passes through the reverse venturi device 15 described above. there is In FIG. 18A a first sorbent introduction point 55 is shown between furnace 47 and ESP 48 . Alternatively, in FIG. 18B a second sorbent introduction point 56 is shown between the FDG unit 49 and the FF unit 50 . Which option is considered the most favorable for the adsorbent depends on the existing structure and plant conditions. Besides the two options shown in Figures 18A-18B, there are many introduction points or combinations of introduction points at which adsorbents can be introduced, and thus these two options are shown for illustrative purposes. The reverse venturi device 15 in FIGS. 18A and 18B is arranged after the FF unit 50 and before the chimney 51 . The reverse venturi device 15 may be constructed according to any of the examples described above as suitable for a variety of applications. Ultimately, the final gaseous emissions exiting the reverse venturi device 15 and released into the atmosphere through the chimney 51 will be able to meet and exceed current and future EPA emissions rules and regulations.

The method illustrated in FIGS. 18A-18B burns fuel in a furnace 47 to produce a pollutant-laden gaseous effluent, flows the gaseous effluent from the furnace 47 into an ESP 48, and uses the ESP 48 to exhaust gas. a step of removing first part particulate contaminants in the article; Using ESP 48 to remove a first portion of the particulate contaminants in the gaseous effluent forms a first concentrate 52 that includes a first portion of the particulate contaminants removed from the gaseous effluent by ESP 48 . In operation, the ESP 48 uses an applied electrostatic charge to remove fine contaminants from the gas exhaust. The method also includes introducing gaseous effluent from ESP 48 to FDG unit 49 and using FDG unit 49 to remove sulfur dioxide contaminants in the gaseous effluent. The step of removing sulfur dioxide contaminants in the gaseous effluent using the FDG unit 49 forms a second concentrate 53 comprising the sulfur dioxide contaminants removed from the gaseous effluent by the FDG unit 49 . The method further includes introducing the gaseous effluent from the FDG unit 49 into an FF unit 50 (i.e., baghouse) and using the FF unit 50 to remove a second portion of the particulate contaminants in the gaseous effluent. include. A third enrichment comprising a second portion of the particulate contaminants removed from the gaseous effluent by the FF unit 50 by removing the second portion of the particulate contaminants in the gaseous effluent using the FF unit 50 An object 54 is formed. In operation, contaminant particles are removed from the gas effluent as it passes through one or more fiber filters (not shown) of the FF unit 50 .

In accordance with the present disclosure, the method further includes the steps of directing the gaseous effluent from the FF unit 50 to a reverse venturi device 15 and using the reverse venturi device 15 to remove heavy metal contaminants in the gaseous effluent. The process of removing heavy metal contaminants in the gaseous effluent using the reverse venturi device 15 causes the gaseous effluent to pass through (ie, flow over) a reactant mass disposed within the reverse venturi device 15 . Amalgam-forming metals within the reactant mass chemically combine with heavy metal contaminants in the gaseous effluent. Thus, the heavy metal contaminants in the reverse venturi device 15 are captured by the reactant mass as they combine with the amalgam-forming metals in the reactant mass. The method further directs the gaseous effluent from the reverse venturi device 15 to a chimney 51 which discharges the gaseous effluent to the surrounding atmosphere. The reverse venturi device 15 has a relatively small footprint and can easily be installed harmoniously between the existing system emission control devices 48, 49, 50 and the chimney 51 to the atmosphere. It is advantageous in terms of

The method may include injecting the sorbent into the gaseous effluent. According to this process, sorbent may be injected into the gaseous effluent at a first sorbent introduction point 55 located between furnace 47 and ESP 48, as shown in FIG. 18A. Alternatively, the sorbent may be injected into the gaseous effluent at a second sorbent introduction point 56 located between the FDG unit 49 and the FF unit 50, as shown in FIG. 18B. The adsorbent includes an amalgam-forming metal and binds at least a portion of the heavy metal contaminants in the gaseous effluent before the gaseous effluent enters the reverse venturi device 15 . By injecting the sorbent into the gaseous effluent at either the first sorbent introduction point 55 or the second sorbent introduction point 56, more mercury, heavy metals and acid gases are released at previously unrealizable levels. It can be collected in the FF unit 50. As mentioned above, the amalgam-forming metal may be selected from the group consisting of zinc, iron and aluminum, and the adsorbent may for example be a CZTS compound. The sorbent can be regenerated and activated so that hazardous pollutants can be collected and recycled.

Referring to FIG. 19, a block diagram of a typical non-gaseous emissions control system is shown. Liquid and/or liquid-like effluent is passed from the fluidized gas desulfurization (FGD) unit 59 and/or from the wet gas scrubber 58 to the lime treatment unit 60 before being sent to the settling tank 61 . After a suitable period of time, this non-gaseous effluent is passed from the settling tank 61 into a pretreatment system or dewatering system 62 for dry waste 64 . Non-gaseous effluents sent through the process of dry waste 64 are prepared for disposal in landfill 65 . The non-gaseous effluent sent through a dewatering system 62, optionally comprising a recirculation system, is prepared for use within a secondary industrial process 63, which may include, for example, gypsum and/or cement production. Non-gaseous effluents from settling basin 61 that are not directed to treatment for dewatering system 62 or dry waste 64 are directed to discharge through drain 66 . The final non-gaseous emissions discharged into this drain 66 are not as regulated as they may be in the years to come. The proposed EPA water effluent rules and regulations are extremely restrictive compared to the effluents that can currently be discharged into drains. Industries that need to discharge contaminated liquid effluents into drains have current effluent control technology that has virtually no chance of meeting and/or complying with upcoming EPA regulations.

Referring to Figure 20, the block diagram of Figure 19 is modified by one or more treatment vessels 67 containing the adsorbents described above. After the non-gaseous effluents are sent from the sedimentation tank 61 and before they are discharged into a drain 66, a treatment tank 67 is placed. The method illustrated in FIG. 20 collects pollutant-laden non-gaseous effluent and passes the non-gaseous effluent through FGD unit 59 and/or wet scrubber 58 to remove some of the contaminants in the non-gaseous effluent. The non-gaseous effluent from the FGD unit 59 and/or the wet scrubber 58 is sent to a lime treatment unit 60, and the non-gaseous effluent is passed through the lime treatment unit 60 to be processed by the Clark process. A step of softening the non-gaseous effluent is included. In operation, lime processing unit 60 removes certain ions (eg, calcium (Ca) and magnesium (Mg)) from the non-gaseous effluent by precipitation. The method comprises sending the non-gaseous effluent from the lime treatment unit 60 to a sedimentation basin 61, precipitating and removing a portion of the contaminants in the non-gaseous effluent, and removing a first portion of the non-gaseous effluent in the sedimentation basin 61. and using the dehydrated by-products in a secondary industrial process 63 to remove a second portion of the non-gaseous effluent from the sedimentation tank 61 and produce a second portion of this non-gaseous effluent in a dry waste treatment 64 Also includes the step of adding In the process of dewatering the first portion of the non-gaseous effluent in the settling tank 61 and utilizing the dehydrated by-product in the secondary industrial process 63, the dewatering step comprises recycling the first portion of the non-gaseous effluent. Secondary industry processes 63 may include, for example, gypsum or cement manufacturing processes. In the step of removing a second portion of the non-gaseous effluent from the settling basin 61 and applying a dry waste treatment 64 to the second portion of the non-gaseous effluent, the dry waste treatment 64 is the second portion of the non-gaseous effluent. into a waste dump 65.

In the present disclosure, the method further includes the step of passing a third portion of the non-gaseous effluent in settling tank 61 to treatment tank 67 containing the disclosed adsorbents. The sorbent contains amalgam-forming metals that bind heavy metal contaminants in the non-gaseous effluent. The sorbent thus captures heavy metal contaminants in treatment vessel 67 as they bind to the sorbent and precipitate/precipitate out of the non-gaseous effluent. The method may then direct the non-gaseous effluent from treatment vessel 67 to drain 66 for discharge. Treatment vessel 67 may be designed to allow non-gaseous effluent (ie, wastewater stream) to flow continuously out of treatment vessel 67 .

Several exemplary embodiments are disclosed for the sorbents disclosed herein. These illustrative embodiments are merely examples and are not meant to represent an exhaustive list of possible variations on this theme.

As noted above, one exemplary sorbent is elemental zinc powder. The zinc powder consists of elemental zinc. Zinc can be used as a powder or as granules. One method used to extend the useful life and reduce and/or prevent pre-oxidation of zinc powder and/or granules used in any gaseous emissions at high temperatures is to is mixed with or coated with solid acids such as sulfamic acid, citric acid and other organic acids. This powder/acid mixture may be injected into the gaseous effluent (eg, flue gas stream) and/or placed in a suitable embodiment of the reverse venturi device 15 .

The optimum particle size for zinc powder ranges from 0.5 nanometers to 7,500 microns. In addition, powder mixtures with different size particle size ranges have been found to be advantageous, particularly when the particle size range is from 0.5 nanometers to 7,500 microns. Similarly, the optimum particle size for zinc granules ranges from 7,500 microns to 3.0 inches. In addition, mixtures of granules having different size particle size ranges have been found to be advantageous, particularly when the particle size range is from 7,500 microns to 3.0 inches.

In another exemplary embodiment, the adsorbent is CZTS with the molecular formula Cu2ZnSnS4. The CZTS may also consist of other phases of copper, zinc, tin and sulfur, which is also advantageous. The CZTS and/or related phases copper, zinc, tin and sulfur may be mixed in stoichiometric proportions followed by mechanochemical compounding in a mill. Additionally, the CZTS may be mixed with either clay, such as bentonite or zeolite, and calcium hydroxide (CaOH) in equal proportions. The optimum particle size for CZTS powder ranges from 0.5 nanometers to 7,500 microns. During testing and development, CZTS powder mixtures with different size particle size ranges have been found to be advantageous, especially when the particle size range is from 0.5 nanometers to 7,500 microns. For applications where special CZTS granules are preferred, the optimum particle size has been found to range from 7500 microns to 3.0 inches. Additionally, mixtures of CZTS granules having different size particle size ranges have been found to be advantageous, particularly when the particle size range is from 7,500 microns to 3.0 inches.

For most contaminants, CZTS is most efficient at the smallest particle size within the range mentioned above and when metallic phase CZTS is present in abundance. Note that copper, zinc, tin, and sulfur are not completely converted to CZTS during the production of CZTS, resulting in a mixture of phases (eg, dambalite (CuZn2) and tin sulfide (SnS)).

In one exemplary method of manufacturing CZTS, copper, zinc, tin, and sulfur are added to the grinder in no particular order. The comminution step is accomplished using a ball mill or some type of attrition comminutor, or a combination of comminution devices used sequentially to obtain the desired particle size. Exemplary particle sizes range from a 325 standard mesh screen to a 100 standard mesh screen (1 standard mesh screen = 7500 microns). The resulting particles are further weighed to a predetermined molar ratio of copper:zinc:tin:sulfur=1.7:1.2:1.0:4.0. After confirming the mesh size and molar ratio, these particles are milled and mechanochemically compounded into CZTS and other phases. Grinding time is controlled for optimum properties depending on the specific application. The pulverization process may be a wet pulverization process in which a suitable solvent such as glycol ether, ethylene glycol, ammonia or other alcohol is added, which is carried out in an inert gas atmosphere, or a dry pulverization process which is carried out in an inert gas atmosphere. can be performed using

During the milling process, intermittent sampling is performed to determine the particle size using a particle size analyzer, SEM, XRD, or to determine the phase transformation ratio using the Raman method. The ball size of the grinder is important and tests have shown that it is optimized when the ball-to-powder weight ratio (charge ratio) is at least 5:1. . The grinding balls are most preferably made of steel, ceramics, zirconia or other material that achieves size and/or phase transformations without contaminating the final product. If wet milling is employed, the CZTS is dried. The CZTS is then mixed using a ribbon blender, V-blender or other suitable mixer to evenly mix the bentonite or zeolite and calcium hydroxide.

According to the method described above, the adsorbent is introduced into the gaseous effluent at a temperature of approximately 750° F. or less. The adsorbent is introduced into the gaseous effluent by any of several methods including, but not limited to, injection, fluidized bed, coated filters and trapping. Installation methods can be selected for ease of installation based on existing emission control systems in the plant. One convenient method is to inject CZTS into the gaseous effluent instead of activated carbon, and the same injection equipment can be used with or without modification.

In some applications, gaseous emissions treatment is optimized when CZTS is mixed with bentonite for effective contaminant removal. Alternatively, treatment of non-gaseous emissions is optimized when CZTS is mixed with zeolites. In addition to the specific materials mixed with the CZTS, the ratio of the mixture may be application specific to provide optimum contaminant removal capabilities.

As shown in FIGS. 18A-18B, when CZTS is used for gaseous effluent treatment, a fiber filter unit 50 is positioned downstream of the CZTS introduction points 55, 56 so that the sorbent particles are captured by the fiber filter unit 50. , to increase the contact time between the gaseous effluent and the adsorbent. Depositing the sorbent on the fiber filters (or bags) of the fiber filter unit 50 allows for longer contact between the gaseous effluent and the sorbent, and allows the sorbent to be collected for subsequent regeneration. can be done. The small particle size of the sorbent allows it to be channeled along the flow of the gaseous effluent much like dust is carried by the wind. During the period in which the adsorbent is entrained in the gaseous effluent stream, the adsorbent contacts contaminants moving in the gaseous effluent stream, thereby causing the contaminants to chemically react and bond with the adsorbent. become. Upon reaching the fiber filter unit 50, while the gaseous effluent continues to pass through the filters in the fiber filter unit 50, the combined adsorbent and contaminant particles are too large to pass through the filter. If the CZTS particles are 10 microns or less, the filter in the fiber filter unit 50 may be pre-coated with larger CZTS particles, activated carbon, talc, lime or other suitable material to prevent the smaller CZTS particles from passing through the filter. may need to. Alternatively, smaller micron size filters may be used in the fiber filter unit 50 .

In other applications for non-gaseous emissions, the CZTS may be introduced into treatment vessel 67 shown in FIG. In this configuration, the CZTS is preferably introduced into the treatment vessel 67 and agitated for a period of time, after which the non-gaseous effluent (eg, waste water) undergoes pH adjustment, flocculation, and filtration prior to discharge. The CZTS in treatment bath 67 may then be subjected to a regeneration step to remove contaminants from the CZTS. Spent CZTS can be regenerated by filtering the mercury from the CZTS or by vacuum distillation. The resulting contaminants can then be used in other industries. CZTS also provides the advantage of being able to reduce nitrate and nitride levels in the non-gaseous effluent.

Effluent regulations set by the EPA and coming into effect in 2016 are much stricter than those for air. Some of the current EPA regulations listed in units of nanograms/liter (ng/L), micrograms/liter (ug/L), and/or grams/L are: Mercury 119 ng/L, Arsenic (As) 8 ug/L, Selenium (Se) 10 ug/L, Nitrogen dioxide (NO2) and Nitrates (NO3) 0.13 g/L. Other heavy metals such as lead (Pb) and cadmium (Cd) are also included in the proposed EPA control levels. In many existing plants, wastewater with pollution levels exceeding acceptable discharge regulations is sent to a reservoir and/or some other type of sludge reservoir. A CZTS can treat solids in a water reservoir in the same way it treats non-gaseous effluents disclosed herein. Depending on the ionic form of the heavy metals, sludge composition and/or pH, the contact time in the CZTS reservoir can be adjusted appropriately. Sufficient pH adjustment, flocculation, and subsequent filtration allow for normal discharge, disposal, and/or other industrial uses, none of which were previously possible.

It should be noted that the sorbents disclosed herein do not contain any free carbon, including activated carbon currently used in the industry. As a result, none of the metal sulfides produced as a by-product of the disclosed method are filtered. These by-products are therefore of high industrial value in gypsum wallboard and cement applications. EPA's metal sulfide filtration tests are well known and well documented for use in these products.

Activated carbon is available in some alternative configurations, but these variations limit the use of activated carbon so that it cannot leak into the effluent. For example, in one example activated carbon is embedded in the filter of the fiber filter unit 50 . This activated carbon does not leak freely into the gaseous effluent stream. As another limited use of activated carbon, it is possible to coat CZTS in crystalline form with activated carbon to produce CZTS with a carbon film thickness of 1.0 nanometers or less. This facilitates the capture of very small mercury metal vapor particles. Similarly, crystalline CZTS can be coated with nanometric zeolite films or other coatings to target specific hazardous contaminants for specific applications. Again, the activated carbon in this variant is not free to leak into the gaseous effluent stream.

Referring to FIG. 21, a graph illustrates the percentage of contaminants removed from emissions by known emission control systems and the percentage of contaminants removed by the reverse venturi device and method disclosed herein. . The EPA currently mandates a 90% pollutant level 78 for gaseous emissions. Existing emission control systems 79 are effective in removing 88% to -90% of hazardous pollutants. However, the EPA has increased the required minimum pollutant removal rate over the years, and many existing emission control systems are unable to meet this requirement, and many other existing emission control systems are: Requirements can only be met when operating at the maximum removal capacity available under current technology.

Still referring to FIG. 21 , an exemplary emission control system 80 is a novel emission control system based on the reverse venturi device, sorbents and/or methods disclosed herein, or the emissions control system disclosed herein. Existing emission control systems modified and enhanced to include reverse venturi devices, sorbents and/or methods. Testing has confirmed that this exemplary emission control system 80 is capable and effective in removing at least 98% of hazardous pollutants, well above current EPA regulatory levels.

22 and 24, one example of an emission control method is illustrated. According to this, when a contaminated gas source 150 is introduced into the system, one or more fluidized bed pre-filters 151, fluidized bed 152, one or more fluidized bed post-filters 153, and system side Passing through the discharge process 154, the gaseous effluent is discharged from the chimney 155 by environmental regulation emissions. It should be noted that it is not always necessary to first pass the contaminated gas source 150 through one or more fluid bed pre-filters 151, but one or more fluid bed pre-filters may be used depending on the requirements of a particular application. 151 may be required.

The fluidized bed 152 has an inverted venturi geometry with a specific length L to diameter D size ratio of at least 2.9:1 and at most 9.8:1. This ratio is optimized to extend the residence time of contaminated gas source 150 in fluidized bed 152 packed with a particular adsorbent such as reactant 164 . Reactant 164 is an adsorbent comprising a copper-zinc-tin-sulfide (CZTS) compound and/or alloys thereof. A preferred length L to diameter D ratio for fluidized bed 152 is 4.4:1, which has been determined by trial and error testing.

Preferably, fluidized bed 152 has a generally curved cross-section. Although not shown in FIG. 24, one or more of the various baffles and/or other application-specific flow restriction obstructions disclosed herein can be incorporated into fluidized bed 152 . Fluidized bed 152 also features generally outwardly extending convex ends 168 and 169 to minimize turbulence through reactant 164 and thereby extend residence time. As the flow of contaminated gas source 150 enters fluidized bed 152 through inlet 165 , it first comes into intimate contact with reactant 164 , resulting in random, non-turbulent flow 166 . Random non-turbulent flow 166 retraces itself by generally outwardly extending convex ends 168 and 169 so that random non-turbulent flow 166 flows through fluidized bed 152 before exiting fluidized bed 152 at outlet 167 . residence time is extended. Reactant 164 promotes random, non-turbulent flow 166 forming a randomly tortuous flow path for contaminated gas source 150 . Note that the length L of fluidized bed 152 does not include convex ends 168 and 169 .

Fluidized bed 152 has a side outlet 170 leading to adsorbent wash station 156 . A sorbent wash station 156 may remove spent sorbent 157 from the system and discard it. Additionally, contaminant elements 158 captured from gas source 150 contaminated with reactant 164 and separated from reactant 164 at adsorbent wash station 156 can be disposed of and/or recycled. Adsorbent wash station 156 can reduce washed reactant 164 to fluidized bed 152 through adsorbent return port 159 . Bulk replenishment sorbent container 168 allows reactant 164 to be replenished as needed to replace spent sorbent 157 that has been removed. According to the system side discharge process 154, the gaseous effluent is discharged from the discharge chimney 155 by environmental regulation discharge. In addition, a discharge of captured waste 160 is also possible.

23 and 24, an example of emission control is illustrated. Accordingly, when a contaminated non-gas source 161 is introduced into the system, one or more fluidized bed pre-filters 151, fluidized bed 152, one or more fluidized bed post-filters 153, and system Through the side discharge process 154 , non-gaseous emissions are discharged by environmental regulation discharge 162 . Note that it is not always necessary to first pass the contaminated non-gas source 161 through one or more pre-fluid bed filters 151, but depending on the requirements of a particular application, one or more pre-fluid bed filters may be used. A positional filter 151 may also be required.

The fluidized bed 152 has an inverted venturi geometry with a specific length L to diameter D size ratio of minimum 2.9:1 and maximum 9.8:1, which ratio is Optimized to extend the residence time of the contaminated non-gas source 161 in the fluidized bed 152 packed with special adsorbents such as. Reactant 164 is an adsorbent comprising a copper-zinc-tin-sulfide (CZTS) compound and/or alloys thereof. A preferred length L to diameter D ratio for fluidized bed 152 is 4.4:1, which has been determined by trial and error testing.

Preferably, the fluidized bed 152 also features generally outwardly extending convex ends 168 and 169 to minimize turbulence through the reactants 164 thereby extending residence time. When a stream of contaminated non-gas source 161 enters fluidized bed 152 through inlet 165 , it first comes into intimate contact with reactant 164 , resulting in random, non-turbulent flow 166 . Random non-turbulent flow 166 retraces itself by generally outwardly extending convex ends 168 and 169 so that random non-turbulent flow 166 flows through fluidized bed 152 before exiting fluidized bed 152 at outlet 167 . residence time is extended. Reactant 164 promotes random non-turbulent flow 166 and forms a randomly tortuous flow path for contaminated non-gas source 161 . Note that the length L of fluidized bed 152 does not include convex ends 168 and 169 .

Preferably, fluidized bed 152 has a generally curved cross-section. Although not shown in FIG. 24, one or more of the various baffles and/or other application-specific flow restriction obstructions disclosed herein can be incorporated into fluidized bed 152 . Fluidized bed 152 has a side outlet 170 leading to adsorbent wash station 156 . A sorbent wash station 156 may remove spent sorbent 157 from the system and discard it. Additionally, contaminant elements 158 captured from non-gas sources 161 contaminated with reactants 164 and separated from reactants 164 at adsorbent wash stations 156 can be disposed of and/or recycled. Adsorbent wash station 156 can reduce washed reactant 164 to fluidized bed 152 through adsorbent return port 159 . Bulk replenishment sorbent container 168 allows reactant 164 to be replenished as needed to replace spent sorbent 157 that has been removed. The system-side exhaust process 154 allows for non-gaseous exhaust through emissions 162 based on environmental regulations. In addition, a discharge of captured waste 163 is also possible.

25, 26, 30 and 31, the contaminated gaseous effluent 250 is filtered through one or more prefilters 251, a fluidized bed 253, one or more postfilters 255, An example method is shown for system side discharge step 256 and final controlled gaseous discharge via discharge stack 257 and/or disposal process 262 . Fluidized bed 253 is bisected by longitudinal plane 290 and portable cradle 271 extends in plane 299 . Inlet P3 and outlet P4 are configured to receive and expel gaseous effluent when fluidized bed 253 is positioned such that longitudinal surface 290 is oriented parallel to surface 299 of portable cradle 271. . Obstructions (not shown) in fluidized bed 253 provide a preferred tortuous flow path that is particularly well suited for gaseous effluent to be introduced through inlet P3 and discharged through outlet P4. Inlet P3 and outlet P4 are located above longitudinal surface 290 of fluidized bed 253 (ie, located on the half side of fluidized bed 253 facing away from portable cradle 271).

The fluidized bed 253 is mounted on a transportable platform 271 of the track 254 . Tilt mechanism 272 is configured to tilt fluidized bed 253 about pivot point 252 between first tilt angle 267 and second tilt angle 277 such that total sweep angle 292 is 96 degrees. When the gaseous effluent is processed in the fluidized bed 253 , the tilting mechanism 272 positions the fluidized bed 253 at a gaseous effluent processing angle 265 such that the longitudinal plane 290 of the fluidized bed 253 is oriented with respect to the plane 299 of the portable cradle 271 . parallel (ie, the angle of inclination between the longitudinal plane 290 of the fluidized bed 253 and the plane 299 of the portable cradle 271 is approximately 0 degrees). It should be noted that when the truck 254 is placed on flat ground, the gaseous effluent treatment angle 265 corresponds to the orientation in which the longitudinal surface 290 of the fluidized bed 253 is substantially horizontal. The tilting mechanism 272 also causes the fluidized bed 253 to reciprocate with respect to a gas effluent treatment angle 265 between a first vibration angle 266 and a second vibration angle 267, and a gas effluent vibration that is a combination of angles 268 and 269. It may be configured to define a sweep angle 270 .

For gaseous effluent, fluidized bed 253 is preferably inclined with an oscillatory sweep angle 270 of 5.5 degrees (angle 268 of 3.0 degrees and angle 269 of 2.5 degrees). The tilting mechanism 272 agitates the fluidized bed 253 between positions 263 and 264 to enhance the effect of the tortuous flow path through the adsorbent within the fluidized bed 253 . It should be noted that although the inventors have found through testing that the angles disclosed above are preferred for treating gaseous emissions, other angles may be employed without departing from the scope of the present disclosure.

In fluid communication with outlet P5 of fluidized bed 253 is an adsorbent wash station 258 where contaminant particles captured by the adsorbent are removed. The removed contaminants can be recycled or disposed of via station 261 . Depleted adsorbent is discarded via station 259, and washed adsorbent is returned from adsorbent return station 260 to fluidized bed 253 via return port P6 for reuse.

27, 28 and 30-32, the contaminated non-gaseous effluent 295 is filtered through one or more prefilters 251, a fluidized bed 253 and one or more postfilters 255. , through a system-side discharge step 256 , and finally as a non-gaseous release 273 based on environmental regulations, and/or through a disposal process 274 . Inlet P2 and outlet P1 are capable of receiving and discharging non-gaseous effluent when fluidized bed 253 is positioned such that longitudinal plane 290 is oriented transversely to plane 299 of portable cradle 271. is. Obstructions (not shown) in fluidized bed 253 provide a preferred tortuous flow path that is particularly well suited for introducing non-gaseous effluents through inlet P2 and outlet P1. Inlet P2 and outlet P1 are bisected by longitudinal surface 290 of fluidized bed 253 (ie, aligned with longitudinal surface 290 of fluidized bed 253).

When the non-gaseous effluent is processed in the fluidized bed 253 , the tilting mechanism 272 positions the fluidized bed 253 at a non-gaseous effluent processing angle 289 such that the longitudinal surface 290 of the fluidized bed 253 is oriented along the plane 299 of the portable cradle 271 . (ie, the angle of inclination between the longitudinal plane 290 of the fluidized bed 253 and the plane 299 of the portable cradle 271 is approximately 90 degrees). It should be noted that the non-gaseous effluent treatment angle 289 corresponds to a substantially vertical orientation of the longitudinal surface 290 of the fluidized bed 253 when the truck 254 is placed on a flat surface. The tilting mechanism 272 also causes the fluidized bed 253 to reciprocally oscillate to a non-gaseous effluent treatment angle 289 between a first oscillating angle 277 and a second oscillating angle 278, and a gaseous effluent treatment angle 289 which is a combination of angles 279 and 280. It may be configured to define an oscillating sweep angle 281 .

For non-gaseous effluent, fluidized bed 253 is preferably inclined with an oscillatory sweep angle 281 of 7.5 degrees (angle 279 of 3.5 degrees and angle 280 of 4.0 degrees). The tilting mechanism 272 agitates the fluidized bed 253 between positions 275 and 276 to enhance the effect of the tortuous flow path through the adsorbent within the fluidized bed 253 . It should be noted that although the inventors have found through testing that the angles disclosed above are preferable for treating non-gaseous emissions, other angles may be employed without departing from the scope of this disclosure. .

In fluid communication with outlet P5 of fluidized bed 253 is an adsorbent wash station 258 where contaminant particles captured by the adsorbent are removed. The removed contaminants can be recycled or disposed of via station 261 . Depleted adsorbent is discarded via station 259, and washed adsorbent is returned from adsorbent return station 260 to fluidized bed 253 via return port P6 for reuse.

29, 30 and 31, when treating aerated sludge-like effluent in a fluidized bed 253, the fluidized bed 253 is positioned at an aerated sludge effluent treatment angle 297 such that the longitudinal surface 290 of the fluidized bed 253 bisects the angle 291 (ie, the angle of inclination between the longitudinal surface 290 of the fluidized bed 253 and the surface 299 of the portable cradle 271 is approximately 45 degrees). Such contaminated sludge-like effluent generally has the characteristics of both gaseous and non-gaseous effluents. Inlet P3 and outlet P4 may be used if these emissions are more like gaseous emissions. Inlet P2 and outlet P1 may be used if these emissions are more like non-gaseous emissions. Application-specific options allow the operator to choose between using inlets P2 and P3 and using outlets P1 and P4.

Referring to Figures 26, 28 and 29, when the sludge-like effluent is naturally aerated and/or thereby enhanced, the effluent is reduced to gaseous and/or non-gaseous effluent. It may flow with a unique property different from For such applications, the tilting mechanism 272 causes the fluidized bed 253 to reciprocally oscillate to an aerated sludge discharge treatment angle 297 between a first oscillation angle 284 and a second oscillation angle 285, and at a combination of angles 286 and 287. It may be configured to define a certain aerated sludge-like discharge oscillatory sweep angle 288 .

For aerated sludge-like effluent, fluidized bed 253 is preferably inclined with an oscillatory sweep angle 288 of about 10 degrees (angle 286 of 5.0 degrees and angle 287 of 5.0 degrees). The tilting mechanism 272 agitates the fluidized bed 253 between positions 282 and 283 to enhance the effect of the tortuous flow path through the adsorbent within the fluidized bed 253 . It should be noted that although the inventors have found through testing that the angles disclosed above are preferable for treating aerated sludge-like emissions, other angles may be employed without departing from the scope of this disclosure. good.

Referring to FIG. 31, the fluidized bed 253 can be agitated by clockwise (not shown) or counterclockwise (shown) rotation 293 . Rotational agitation 293 can be set to a range of rotational speeds depending on the particular application. Agitation can be further enhanced by reciprocating the fluidized bed 253 between a first radial position 295 and a second radial position 296 to define a radial vibration angle 294 and rotationally vibrating the fluidized bed 253 . can. The cycle rate of the rotational oscillation by the radial oscillation angle 294 can be set to a range of amplitudes and/or arc lengths depending on the particular application.

Other agitation methods (not shown) suggested for application to the fluidized bed 253 include external vibration exciters, internal ultrasonic vibrators, heating systems, and/or similar systems. Additionally, by disrupting the flow of effluent by programming the valving device to create a pulse-like disturbance in the flow of effluent prior to entering the fluidized bed 253 and/or Further agitation of the flow (not shown) can be achieved by disrupting the flow of effluent at the outlet of bed 253 .

Referring to FIG. 33, a matrix is shown in which the disclosed preferred reactive CZTS alloy sorbent 341 is compared to other sorbents such as activated carbon 342 and zeolite 343 . Nitrogen 368, phosphates 369, heavy metals 370, sulfur 371, mercury 372, and selenate 373 are listed as major types of contaminants 367 in the table. Further, contaminants 367 are described such that each adsorbent is listed for gaseous emissions 344, 346 and 348 as opposed to non-gas emissions 345, 347 and 349. FIG.

Reactive CZTS alloy sorbent 341 has been tested and found to be effective in capturing and removing contaminants 367 in gaseous 344 and/or non-gaseous 345 effluents. On the other hand, activated carbon 342 is not effective in capturing or removing contaminants 367 in gaseous effluent 346 and/or non-gaseous effluent 347 . Similarly, zeolite 343 is also ineffective at trapping or removing contaminants 367 in gaseous effluent 348 and/or non-gaseous effluent 349 .

Referring to FIG. 34, an expanded list of sorbents is shown, including reactive CZTS alloy sorbents 351 and other sorbents such as Caustics 350 and ferric oxide 355 and zeolites 356 of the present disclosure. Reactive CZTS alloy adsorbents 351 include sulfur (S) CZTS alloy 352, selenate (S) CZTS alloy 353, and ferrous oxide CZTS alloy 354.

The CZTS alloy adsorbent 351 generally reacts effectively with the following contaminant groups. selenate 357, fully ionized sulfur 358, fully ionized nitrogen 359, and fully ionized phosphate 360. Reactive CZTS alloy sorbent 351 is capable of capturing and removing these contaminants from both gaseous and non-gaseous emissions.

On the other hand, the caustic agent 350 is only effective against fully ionized sulfur 358. Ferric oxide 355 is effective only for selenate 357 and has very slow reactivity (and works only for non-gaseous emissions) for fully nitrogen 359 and fully ionized phosphate 360 . Zeolite 356 is effective only for fully ionized nitrogen 359 and fully ionized phosphate 360 .

As a result, known sorbents such as cauterizing agent 350, ferric oxide 355, and zeolite 356 are less effective than the broad-spectrum properties of the reactive CZTS alloy sorbent 351 disclosed herein. characteristics) are limiting. Even if known sorbents have a certain level of effectiveness, none fall short of the level of effectiveness of the reactive CZTS alloy sorbent 351 disclosed herein.

Referring to FIG. 35, matrix 364 shows that existing sorbents 365 capture and remove contaminants 367 such as nitrogen 368, sulfur 369, phosphorus 370, heavy metals 371, mercury 372 and selenate 373 in emission control systems. Indicates whether it can be post-processed after being used in Separation of these contaminants 367 from prior art sorbents in gaseous effluent 374 and/or non-gaseous effluent 375 is very unlikely, except for nitrogen 368 in gaseous effluent 374. .

Matrix 364 also shows that the potential for reuse of existing adsorbent 366 after separation of contaminants 367 is practically improbable, with the exception of gaseous effluent 376 containing nitrogen 368 .

Referring to FIG. 36, matrix 378 shows that the reactive CZTS alloy sorbent 339 disclosed herein has nitrogen 368, sulfur 369, phosphorous 370, heavy metals 371, mercury 372 and selenate 373 in an emission control system. After being used to capture and remove contaminants 367 such as, can it be post-processed? It would be particularly advantageous to be able to separate contaminants 367 in gaseous effluent 374 and/or non-gaseous effluent 375 from the disclosed reactive CZTS alloy sorbent 339 . This is because contaminants 367 can thereby be disposed of or recycled more quickly, and reactive CZTS alloy sorbent 339 can be reused in the emissions control system (as shown by matrix 378).

Specifically, is matrix 378 reusable after reactive CZTS alloy sorbent 340 disclosed herein is separated from contaminants 365 in gaseous effluent 376 and non-gaseous effluent 377? indicates The gaseous emissions 250 are monitored and analyzed at step 379 to determine the types and levels of contaminants in the gaseous emissions 250 . Monitoring can be performed by statistical intermittent spot checks performed at regular intervals or by continuous in-line monitoring and analysis. Based on the type and/or level of contaminants in the gaseous effluent 250 determined in step 379, the gaseous effluent 250 is further passed through the appropriate pre-filters 381, 382, 383 and/or 384. The material stream is sent to the prefilter inlet manifold 380 . Selection of appropriate prefilters 381, 382, 383 and/or 384 is accomplished by the selection method illustrated in FIG.

Referring to FIG. 37, a block diagram illustrates a system and method for removing contaminants from gaseous exhaust 250. As shown in FIG.

The prefilter shown in FIG. 37 is filled with reactive CZTS alloy adsorbent 351 shown in FIG. For example, the prefilter 381 is filled with sulfur (S) CZTS alloy 352 shown in FIG. The prefilter 382 is filled with selenate (S) CZTS alloy 353 shown in FIG. The prefilter 383 is filled with ferrous oxide CZTS alloy 354 shown in FIG. A prefilter 384 is filled with a combination of CZTS alloy adsorbents 352, 353 and/or 354.

Additional prefilters, each filled with a different combination of CZTS alloy sorbents 352, 353 and/or 354, are added to the prefilter inlet manifold 380 and cooperate to identify contaminants in the gaseous effluent 250. Levels and/or types can be effectively handled.

Contaminated gaseous effluent 250 is passed through a suitable prefilter and then through a fluidized bed 253 by prefilter outlet manifold 385 . For gas exhaust 250 , the enclosure of fluidized bed 253 is oriented substantially parallel to cradle 271 . Contaminants are separated from the adsorbent in step 258 and returned to fluidized bed 253 via adsorbent return port 260 .

After the gaseous effluent 250 exits the fluidized bed 253, a post-filter monitoring step 386 determines the new level and/or type of contaminants remaining in the gaseous effluent 250, and the gaseous effluent 250 passes through the post-filter inlet. It is passed through manifold 387 . Selection of appropriate post-filters 388, 389, 390 and/or 391 is accomplished by the selection method illustrated in FIG. The post-filter shown in FIG. 37 is filled with reactive CZTS alloy adsorbent 351 shown in FIG. For example, the post filter 388 is filled with sulfur (S) CZTS alloy 352 shown in FIG. The post filter 389 is filled with selenate (S) CZTS alloy 353 shown in FIG. The post filter 390 is filled with ferrous oxide CZTS alloy 354 shown in FIG. A post filter 391 is filled with a combination of CZTS alloy adsorbents 352, 353 and/or 354. Post filter outlet manifold 392 directs gaseous exhaust 250 to gas system side exhaust step 256a. In the same process, a portion of the gaseous effluent 250 is discharged into a controlled gas discharge chimney 257 and another portion of the gaseous effluent 250 is discharged via a suitable waste disposal process 262. be.

Additional post-filters, each filled with a different combination of CZTS alloy sorbents 352, 353 and/or 354, are added to the post-filter inlet manifold 387 and cooperate to reduce specific levels and/or in the gaseous effluent 250. or types of contaminants can be effectively treated.

All of the pre-filters 381 , 382 , 383 , 384 and post-filters 388 , 389 , 390 , 391 may go through the sorbent wash step 258 and the sorbent return port 260 separately. At step 258 , the contaminants are separated from the CZTS alloy sorbent 351 so that the contaminants can be recycled and/or properly collected for disposal 261 . Spent CZTS alloy sorbent 351 can be disposed of via disposal step 259 . After step 258, replacement of the specific CZTS alloy sorbent 351 may be performed to the specific pre-filters 381, 382, 383, 384 and/or post-filters 388, 389, 390, 391. FIG. 11 illustrates a specific path diagram and/or schematic representation of the sorbent from the pre-filters 381, 382, 383, 384 and/or the post-filters 388, 389, 390, 391 to/from the sorbent wash step 258; is omitted.

Referring to FIG. 38, a block diagram illustrates systems and methods for removing contaminants from non-gaseous emissions 295 . The non-gaseous effluent 295 is monitored and analyzed at step 379 to determine the types and levels of contaminants in the non-gaseous effluent 295 . Monitoring can be performed by statistical intermittent spot checks performed at regular intervals and/or continuous in-line monitoring and analysis. Based on the type and/or level of contaminants in non-gaseous effluent 295 determined in step 379, non-gaseous effluent 295 may be further passed through appropriate pre-filters 381, 382, 383 and/or 384. Also, the effluent stream is directed to the prefilter inlet manifold 380 . Selection of appropriate prefilters 381, 382, 383 and/or 384 is accomplished by the selection method illustrated in FIG.

The prefilter shown in FIG. 38 is filled with a reactive CZTS alloy adsorbent shown in FIG. For example, the prefilter 381 is filled with sulfur (S) CZTS alloy 352 shown in FIG. The prefilter 382 is filled with selenate (S) CZTS alloy 353 shown in FIG. The prefilter 383 is filled with ferrous oxide CZTS alloy 354 shown in FIG. A prefilter 384 is filled with a combination of CZTS alloy adsorbents 352, 353 and/or 354.

Additional pre-filters, each filled with a different combination of CZTS alloy sorbents 352, 353 and/or 354, are added to pre-filter inlet manifold 380 to work together to achieve specific levels and and/or types of contaminants can be effectively treated.

After the contaminated non-gaseous effluent 295 is passed through the prefilter, the prefilter outlet manifold 385 passes the effluent to the fluidized bed 253 . For non-gaseous effluent 295 , the enclosure of fluidized bed 253 is oriented substantially perpendicular to pedestal 271 . Contaminants are separated from the adsorbent in step 258 and returned to fluidized bed 253 via adsorbent return port 260 .

After the non-gaseous effluent 295 exits the fluidized bed 253, a post filter monitoring step 386 determines the new level and/or type of contaminants remaining in the non-gaseous effluent 295, and the non-gaseous effluent 295 is through a stationary filter inlet manifold 387 . Selection of appropriate post-filters 388, 389, 390 and/or 391 is accomplished by the selection method illustrated in FIG. The post-filter shown in FIG. 38 is filled with reactive CZTS alloy adsorbent 351 shown in FIG. For example, the post filter 388 is filled with sulfur (S) CZTS alloy 352 shown in FIG. The post filter 389 is filled with selenate (S) CZTS alloy 353 shown in FIG. The post filter 390 is filled with ferrous oxide CZTS alloy 354 shown in FIG. A post filter 391 is filled with a combination of CZTS alloy adsorbents 352, 353 and/or 354. Post-filter outlet manifold 392 directs non-gaseous exhaust 295 to non-gas system side exhaust 256b. In the same process, a portion of the non-gaseous effluent 295 is released as an environmentally controlled non-gaseous emission 273 and another portion of the non-gaseous effluent 295 is sent to a suitable waste disposal process 262. emitted through

Additional post-filters, each filled with a different combination of CZTS alloy sorbents 352, 353 and/or 354, are added to post-filter inlet manifold 387 to work together to achieve specific levels and and/or types of contaminants can be effectively treated.

All of the pre-filters 381 , 382 , 383 , 384 and post-filters 388 , 389 , 390 , 391 may go through the sorbent wash step 258 and the sorbent return port 260 separately. At step 258 , the contaminants are separated from the CZTS alloy sorbent 351 so that the contaminants can be recycled and/or properly collected for disposal 261 . Spent CZTS alloy sorbent 351 can be disposed of via disposal step 259 . After step 258, replacement of the specific CZTS alloy sorbent 351 may be performed to the specific pre-filters 381, 382, 383, 384 and/or post-filters 388, 389, 390, 391. Illustrative Path Diagrams and/or Schematic Illustrations of Adsorbent from Pre-Filters 388, 389, 390, 391 and/or Post-Filters 388, 389, 390, 391 to/from Adsorbent Wash Step 258 is omitted.

It should be noted that although steps in the method are described and illustrated in a particular order, these steps may vary without departing from the scope of the present disclosure, unless the order of the steps is otherwise stated. They may be performed in order. Similarly, the methods described and illustrated herein can be practiced without all of the above steps, or with additional intermediate steps not described, without departing from the scope of this disclosure. .

It will be evident in light of the above disclosure that the present invention is capable of many variations and may be practiced otherwise than as specifically described within the scope of the appended claims. These preceding statements should be construed to cover any combination in which the inventive novelty would be useful. Use of the word "the" in an apparatus claim indicates an antecedent basis that is an active claim intended to be included within the scope of the claim; Words precede terms that are not intended to be included in the claims.

Claims (18)

An effluent control system having a fluidized bed device for removing contaminants from effluent, comprising:
an inlet portion having an inverted venturi shape, into which the discharged matter flows in at a predetermined inlet flow velocity; an outlet portion, through which the discharged matter is discharged at a predetermined outlet flow speed; an enlarged diameter portion that captures the contaminants in the effluent;
the inlet portion, the outlet portion, and the enlarged diameter portion of the housing are in fluid communication with each other;
a mass of reactant is disposed within the enlarged diameter portion of the housing;
the reactant mass has a reactive outer surface positioned in contact with the effluent;
The reactant mass contains an amalgam-forming metal that chemically bonds with at least a portion of the contaminant in the effluent reaching the reactive outer surface of the reactant mass through the enlarged diameter portion of the housing. contained on the reaction outer surface, the reactant mass comprising a copper-zinc-tin-sulfide (CZTS) compound;
The emission control system includes:
at least one pre-filter in fluid communication with the fluidized bed apparatus and positioned upstream of the fluidized bed apparatus with respect to the effluent flow; or
at least one post filter in fluid communication with the fluidized bed apparatus and positioned downstream of the fluidized bed apparatus with respect to the effluent flow;
The emission control system of claim 1, wherein said at least one pre-filter or said at least one post -filter includes an adsorbent comprising an alloy of copper-zinc-tin-sulfide (CZTS) compounds. 2. The effluent control system of claim 1, wherein said fluidized bed apparatus is permanently installed on site. 2. The effluent control system of claim 1, wherein said fluidized bed apparatus is mobile. 2. The effluent control system of claim 1, wherein the fluidized bed apparatus has a longitudinal surface oriented substantially horizontally when intended for gaseous effluent. 2. The effluent control system of claim 1, wherein the fluidized bed apparatus has a substantially vertically oriented longitudinal surface when intended for non-gaseous effluent. 2. The emission control system of claim 1, wherein the alloy of copper-zinc-tin-sulfide (CZTS) compounds includes at least one of sulfur, selenate and iron. object control system. An emission control method for removing contaminants from an emission, comprising:
passing the effluent through an inverted venturi fluidized bed apparatus containing reactants that chemically bond with heavy metal contaminants carried by the effluent;
entrapping the heavy metal contaminants in the reactants contained within the inverted venturi fluidized bed apparatus;
The emission control method includes:
passing said effluent prior to being sent to said inverted venturi fluidized bed apparatus through at least one prefilter having a prefilter adsorbent comprising an alloy of copper-zinc-tin-sulfide (CZTS) compounds; process,
passing said effluent from said inverted venturi fluidized bed device through at least one post-filter having a post-filter adsorbent comprising an alloy of copper-zinc-tin-sulfide (CZTS) compounds; or ,
A method of controlling emissions, further comprising a combination of these steps. 8. The method of claim 7, wherein the alloy of copper-zinc-tin-sulfide (CZTS) compounds comprises at least one of sulfur, selenate and iron. 8. The method of claim 7, wherein the alloy of copper-zinc-tin-sulfide (CZTS) compounds comprises an alloy of a copper-zinc-tin-sulfide (CZTS) compound and sulfur; A method comprising an alloy of a tin-sulfide (CZTS) compound and selenate and an alloy of a copper-zinc-tin-sulfide (CZTS) compound and iron. 8. The method of claim 7, wherein said pre-filter sorbent and said post-filter sorbent are all made from an alloy of said copper-zinc-tin-sulfide (CZTS) compounds of the same composition. A method characterized by 8. The method of claim 7, wherein said pre-filter sorbent and said post-filter sorbent are made from alloys of said copper-zinc-tin-sulfide (CZTS) compounds of different compositions. A method characterized by 8. The method of claim 7, wherein
identifying the type and amount of contaminants that passed through the at least one pre-filter;
determining which pre-filter sorbent to select based on the identified contaminant type and quantity. 13. The method of claim 12, wherein identifying the type and amount of contaminants that have passed through the at least one prefilter is performed intermittently at regular intervals. . 13. The method of claim 12, wherein identifying the type and amount of contaminants that have passed through the at least one pre-filter is performed continuously. 8. The method of claim 7, wherein
identifying the type and amount of contaminants that passed through the at least one post-filter;
determining which post-filter sorbent to select based on the identified contaminant type and quantity. 16. The method of claim 15, wherein identifying the type and amount of contaminants that have passed through the at least one post-filter is performed intermittently at regular intervals. . 16. The method of claim 15, wherein identifying the type and amount of contaminants that have passed through the at least one post-filter is performed continuously. 8. The method of claim 7, wherein
separating the pre-filter sorbent and/or the post-filter sorbent from the contaminants captured and removed from the effluent;
after separating the contaminants from the pre-filter sorbent and/or the post-filter sorbent, returning the pre-filter sorbent to the at least one pre-filter and/or the post-filter sorbent; to said at least one post-filter, and recycling said pre-filter sorbent and/or said post-filter sorbent.

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