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Issues and Challenges in Sustainable Solid Waste Management
Published in Rajeev Pratap Singh, Vishal Prasad, Barkha Vaish, Advances in Waste-to-Energy Technologies, 2019
Agamuthu Pariathamby, Mehran Sanam Bhatti
Anaerobic digestion is the second most economical WTGE technology. Despite anaerobic digestion being economical, it is still less prevalent in developing countries as compared to developed countries. The reason behind the less execution of anaerobic digestion is the lack of regulations on separate treatment of organic waste or lack of national targets or policies on organic waste reuse, and cheaper landfill fee (Edwards et al., 2015). The gate fee or landfill fee is a very effective mechanism in some developed countries to divert waste from landfills to incineration or anaerobic digestion. It is often discussed that landfill fee or levies can provide three benefits such as (1) incentive to reduce and recycle waste streams such as organic waste or dry recyclables, (2) provide funds for costs-related operation of landfills, end of life, and of externality mitigation of landfill sites, and (3) generate revenue for alternative SSWM infrastructure (Edwards et al., 2015). However, adoption of landfill fee or levies must be carried out with great caution as it can backfire in the form of illegal dumping of waste in open dumps in developing countries. Similar reports have been highlighted for CDW as the cost of transport (in case of long distances between construction sites and landfills) and landfilling is high.
Waste-to-Energy Investment Evaluation (WTE Tool)
Published in Efstratios N. Kalogirou, Waste-to-Energy Technologies and Global Applications, 2017
Revenues in a WTE facility mainly come from two sources. The first income source is the so-called gate fee (also known as a tipping fee). The gate fee is the amount of money paid, usually per ton of waste, in order for waste to pass through the “gate” and be processed in the WTE facility. Think of a gate fee as analogous to tolls on a highway, a ticket for a performance, or a service. A gate fee is paid by waste producers, which are primarily municipalities (providing Municipal Solid Waste [MSW]) and, secondarily, large producers (such as factories, commercial parks, airports, etc.) that are obliged to handle their own waste (industrial or commercial waste similar to MSW) at their own cost according to the polluter pays principle. Input values required for gate fee annual revenue stream calculations are: Gate fee in currency per quantity unit (e.g., USD/ton)Annual delivered tonnage in quantity unit per year (e.g., ton/yr)
Ethanol production from food waste in West Attica: evaluation of investment plans under uncertainty
Published in Biofuels, 2020
A. Konti, P. Papagiannakopoulou, D. Mamma, D. Kekos, D. Damigos
The quantity of food waste is 375 kg/household/year or 84,420 tonnes/year, given the fact that food waste accounts for approximately 28% of total MSW [22]. The electricity consumption of an average dryer of 5 L is 1.1 kWh/kg and the price of electricity is 0.095 €/kWh. Therefore, the cost of drying is estimated at 39.19 €/household/year, or 8,822,000 € in total. Households participating in the program will be reimbursed for the electricity cost of drying by the operator of the plant after subtracting the existing cost of MSW management. To wit, households will be reimbursed for the electricity cost partially by the corresponding municipality that will continue to pay the same price as today for the management of the MSW, and partially by the operator of the bioethanol production plant. More explicitly, the MSW transportation cost is 15 €/tonne [23]. Further, the gate fee for the landfill is 45 €/tonne [23] and the special burial fee for the waste is 35 €/tonne [24]. If the food waste should be transferred and buried in the landfill (in the absence of the ethanol production plant) the cost charged to the households would be around 8,020,000 €/year. To this end, the reimbursement that represents for the plant the price of the raw material is estimated at 802,000 €/year.
Co-treatment of leachate in municipal wastewater treatment plants: Critical issues and emerging technologies
Published in Critical Reviews in Environmental Science and Technology, 2021
Recep Kaan Dereli, Eoghan Clifford, Eoin Casey
Moreover, the main cost components that are expected to increase in WWTP operation are chemicals (pH regulation, external carbon), energy (additional air demand, pumping, sludge processing) and management (labor, monitoring and maintenance). Ye at al. (2014) reported that the reagent and operational costs would be 1.65 and 2.65 $/m3, respectively, when leachate is pretreated by using coagulation and flocculation with FeCl3 and CaO in a WWTP site in China. The Environment Agency of the UK reported the total operational expenditure (plant operation, maintenance, reagent, transport and discharge costs) of leachate co-treatment as 15.4-17.5 £/m3 (Environment Agency, 2007). When leachate was discharged into sewer system, the cost of co-treatment in publicly owned WWTPs was calculated as 10 $/m3 in USA (Staley & Bolyard, 2018). The Environmental Protection Agency (EPA) of Ireland (2013) estimated the average marginal cost of leachate treatment in a WWTP to vary between 0.83 and 1.89 €/m3. WWTPs co-treating leachate may apply a gate fee based on leachate volume and/or pollutant load to off-set the increase in operational costs. Meeroff and Teegavarapu (2010) reported a landfill that discharged leachate to a WWTP was charged 0.84 $/m3 for co-treatment. The EPA (2013) stated that landfill operators in Ireland were paying a gate fee ranging from zero charge to 25 €/m3. The tariff structure was generally based on volume, but there were a few cases with COD and ammonium load based pricing. Considering the high variations in leachate properties, WWTP configuration and discharge limitations, a techno-economic feasibility study must be carried out in case by case basis before deciding acceptance of leachate in a WWTP.