- freely available
Sustainability 2013, 5(12), 5333-5346; doi:10.3390/su5125333
Abstract: The planning actions in municipal solid waste (MSW) management must follow strategies aimed at obtaining economies of scale. At the regional basin, a proper feasibility analysis of treatment and disposal plants should be based on the collection and analysis of data available on production rate and technological characteristics of waste. Considering the regulations constraint, the energy recovery is limited by the creation of small or medium-sized incineration plants, while separated collection strongly influences the heating value of the residual MSW. Moreover, separated collection of organic fraction in non-densely populated area is burdensome and difficult to manage. The paper shows the results of the analysis carried out to evaluate the potential energy recovery using a combined cycle for the incineration of mechanically pre-treated MSW in Basilicata, a non-densely populated region in Southern Italy. In order to focalize the role of sieving as pre-treatment, the evaluation on the MSW sieved fraction heating value was presented. Co-generative (heat and power production) plant was compared to other MSW management solutions (e.g., direct landfilling), also considering the environmental impact in terms of greenhouse gases (GHGs) emissions.
|c||constant pressure specific heat||β||pressure ratio||f||gases|
|HV||heating value||ηI||first-principle yield||g||gas|
|k||adiabatic law exponent||ηII||second-principle yield||g-g||gas-gas heat exchanger|
|m||mass flow||η||total efficiency||GT||gas turbine|
|n||air index||χ||coefficient||g-w||gas-water heat exchanger|
|Q||co-generated thermal power||Δ||finite difference||st||steam|
|W||electrical power||ae||air in excess||w||water|
|Y||Yield||at||theoretical air||0, 1, 2, 3, 4, 5, 6, 7, 8, 9 calculation section|
The main objective in integrated solid waste management (ISWM) [1,2] is to implement technologies that reduce the environmental pressure by recovering both the fractions with a considerable value on the market and the non-traditional ones (e.g., organic [3,4,5,6,7,8], medical [9,10,11], automotive shredder residues , WEEE ). Moreover, any good management system also includes the involvement of the people, who have to be aware of the environmental benefits and of the reduced danger to health that results from a correct behavior [14,15]. Such an objective is highlighted by European Union (EU) legislation, which produced several Directives on waste disposal, treatment and incineration [16,17,18,19]. Such Directives: (i) prohibit waste recovery and disposal that have a negative impact on both the human health and the environment; (ii) aim at the reduction of waste production as well as the promotion of the reuse, the recycling and the recovery activities. The Italian Government acknowledged these Directives [20,21], also imposing the energy recovery from waste incineration.
According to the above-mentioned regulations and principles, the ISWM should both reduce landfilling and increase energy and materials recovery in order to lower environmental impact, energy resources consumption and economic costs. For example, landfilling of energy-rich waste should be avoided as far as possible, partly because of the negative environmental impacts of the technique, but mainly because of the low resources recovery .
Various types of Life-Cycle-Analysis (LCA) have been proposed for determining the most environmental-sound ISWM procedure [23,24]. Most of them focus on high percentages of separated collection in relatively small and densely populated area: some examples are described in [25,26,27,28]. However, in a scarcely-populated area, the environmental (e.g., GHG emissions) and economic impact of MSW collection is high because of fuel consumption [25,29,30]. The ISWM issue in a non-densely populated area concerns developing and developed countries. For example, 60% of EU surface has a population density of less than 100 inhab km−2 .
In order to reduce the landfill volumes as well as to close the MSW cycle, a solution can be the waste incineration with energy recovery . Therefore, excluding direct landfilling of MSW, the solutions for ISWM are essentially three (Figure 1): direct burning of the raw MSW; accelerated stabilization of the whole MSW prior to incineration; MSW mechanical pre-treatment with secondary fuel (or RDF) production prior to incineration and organic matter aerobic stabilization (the so-called biostabilization) before landfilling.
Regarding the last solution, the mechanical pre-treatment of waste by sieving has aroused great interest, because it influences the MSW volumes addressed for both incineration and landfilling ; as consequence, the process reduces the environmental impact of the whole ISWM system. Sieving is carried out on raw waste and it allows separating out a flow of material that is characterized by a higher energy content (heating value, HV, and net calorific value, NCV) . The separation leads to a reduction in the combustion section, even if it partly penalizes the energy recovery. Moreover, in plants which treat waste coming from basins with different waste management policies, the pre-treatment process allows to guarantee a better quality of secondary fuel.
The case study presented in this paper regards the methodological approach applied to determine which technical solution may be proposed for solving some ISWM issues in a non-densely populated area, with specific reference to Basilicata, an Italian region. The analysis of the MSW composition and quantity (current situation and future trend) has been carried out. The results, combined with the waste size characterization, allowed to define the optimal mechanical pre-treatment in order to achieve an optimal balance between GHGs emissions and heat-and-power production.
2. Materials and Methods
2.1. Investigated Area
Basilicata is a predominantly mountainous region (Figure 2a) that covers about 10,000 km2 in the center of Southern Italy. The population is less than 580,000 inhabitants . Most of the 131 districts have a population below 3000 inhab with an average population density varying between 31 and 380 inhab km−2 (average: 57 inhab km−2; Figure 2b).
The average MSW production (1.08 kg inhab−1 d−1) is less than the national average [36,37]. During the last few years, a 2% y−1 increase in the MSW average production occurred, with peaks of 5% y−1 in the largest towns.
2.2. Characteristics of Waste Production
A survey was carried out with the aim of determining both the sieved waste composition and the influence on the combustible waste characteristics . The mesh size was determined by considering that it has a considerable effect on the quantity of the obtainable energy .
Experimental tests were carried out on the waste collected in urban centers, with a production rate that fell in the range 0.8–1.2 kg inhab−1 d−1. The percentages of separation by sieving were determined experimentally and the different product fraction percentages were deduced on the basis of the average composition of the waste. The data was determined as a function of the amount, in terms of weight, of the individual fractions of over-sieved (OS) and under-sieved (US) waste. This data can be extended to all compositions, on the assumption that if the amount, in terms of weight, of the single fraction is varied, the size does not change. Predictions in MSW evolution concerning quantity and composition were carried out considering: (i) past data; (ii) population growth; (iii) evolution of policies regarding separated collection .
The HV of each fraction was estimated using data found in scientific literature [32,39] (organic: 2,930.2 kJ kg−1; paper: 12,558.0 kJ kg−1; plastic and rubber: 20,930.0 kJ kg−1; wood, textile and leather: 15,488.2 kJ kg−1; under-sieved waste below 20 mm: 5,651.1 kJ kg−1) and was applied to each OS fraction in order to obtain the respective energy content.
2.3. Environmental Effects Assessment
The GHGs emission assessment of three ISWM possible solution was carried out considering the influence of the sieve cut-off . Such solutions are: (a) the direct MSW landfilling; (b) US landfilling and OS incineration; (c) US biostabilization and OS incineration. Table 1 reports the emission factors assumed for the environmental assessment [40,41].
|Biostabilization||without energy recovery||kg CH4eq kg−1 biodegradable VSS||2.5|
|with energy recovery||1.5|
|Incineration plant||50% of biodegradable fraction removal||kg CH4eq kg−1 VSS||1.5|
|Landfilling (50% of biogas capture)||without energy recovery||kg CH4eq kg−1 biodegradable VSS||10.5|
|with energy recovery||9.5|
2.4.1. Process and Model Description
The combined gas-steam power cycle plant (Rankine-Brayton cycle ) for power and heat production may be regarded as one of the best strategies for MSW management, in terms of efficiency, pollution and management costs [43,44,45]. The layout of the examined plant is shown in Figure 3.
The thermal cycle used for power recovery is composed of a gas turbine coupled with a water steam cycle, where the heat entering the steam cycle is obtained from the thermal recovery carried out on the gas turbine exhaust. Before being sent for treatment, the high-temperature combustion gases go through a heat exchanger, where heat is transferred, and what comes out is a liquid at a lower temperature. Then the heated and compressed air is sent to the gas turbine. The emitted gases are introduced into a steam generator. A mono-phase counter-pressure steam turbine was considered. The plant is completed by an electrical power generator and by the heat exchangers for producing hot water. Moreover, the plant includes a condensate collector, centrifuge pumps and a degasser for treating the condensate water and the steam. For the gas-gas heat exchanger a Ljungström-type rotating system  was used.
In the case of combustion under practical conditions (n > 1), the exhaust gas discharge is equal to:
In order to calculate the above terms, we used the following equations:
If there are no unburned substances, and no heat exchange between the gases and the combustion chamber, the gas temperature only depends on the fuel characteristics, the air index n as well as the initial air and fuel temperatures. In practice, a temperature Tf equal to the theoretical combustion temperature, Tad, is considered:
The temperature of the gas entering the turbine is given by the equation below, by accepting for the gas-gas exchanger an efficiency of εg-g:
The temperature of the gas leaving the turbine, considering the 3-4 adiabatic transformation (Figure 3) as reversible, is given by the following equation:
The electrical power, produced by the alternator coupled to the gas turbine, is given by the equation:
With an efficiency of the air-water heat exchanger of εg-w, the steam discharge in the turbine is:
Considering a total efficiency ηST for the steam turbine section, the electrical power developed is:
The steam/water heat exchanger operates with a gradient of ΔT7–6.
The co-generated thermal energy is equal to:
A water discharge is transferred, and is equal to:
The first-principle yield of the co-generative combined cycle plant (ηI) is:
The yield is lower because a part of Q is wasted while it is transported to the heating.
In co-generative plants, we also consider a second-principle yield (ηII) which takes into account that the quantity of electrical power is much greater than the thermal power.
The analyzed energy is intended as the work, which can be obtained as a system returns to steady conditions. In the components of work production, the energy flow coincides with the electrical power; in the condenser, the energy flow is lower than the thermal flow because of the increase in the exchange fluid entropy. The available energy entering the plant coincides with the thermal power produced by the waste combustion. In the case of electricity generation only, ηII is equivalent to ηI. In the case of co-generation we have:
In order to use the waste heating value as a heating source for summer air-conditioning, we consider a value Y for the refrigeration yield; therefore we have:
2.4.2. Data and Assumptions
The waste-to-energy plant is:
intended to produce power and low temperature heat for feeding a heating network;
situated in a strategic area that can be reached from every town through the ordinary communication routes;
provided with a landfill in order to reduce the transportation of residual waste (e.g., ash, slag).
The HV of the secondary fuel used in the incineration plant results from the MSW analysis.
Table 2 shows the values of the parameters used in the calculation.
|Coefficients||theoretical combustion air (mat/msw)||-||4.300|
|air index (n)||-||2.300|
|Production rates||slag (χsg)||kg kg−1||0.055|
|flying ash (χfa)||kg kg−1||0.188|
|Specific heats||gases||kJ kg−1 K−1||1.260|
|gas entering the turbine||kJ kg−1 K−1||1.009|
|gas leaving the turbine||kJ kg−1 K−1||1.165|
|steam entering the turbine||kJ kg−1 K−1||1.091|
|Yield||heat exchanger||gas-gas (εg-g)||-||0.950|
|refrigerating machine (Y)||-||0.800|
The combustion gas temperature, Tf , is 95 °C.
3. Results and Discussion
3.1. Waste Production and Energy Potential Evolution
Figure 4 shows the estimation of waste production as a function of different percentages of separated waste collection.
In the next 25 years the MSW production will increase almost linearly, reaching values of 420 and 600 t y−1 considering, respectively, the optimistic (35%) and the pessimistic (7%) percentages of separated collection.
Concerning the current composition (Table 3, second column), the MSW production varies greatly. The amount of biodegradable organic waste is equal to about 0.350 kg inhab−1 d−1, while the maximum level of paper and plastic collection is 50% of the national average. In the next decade, Basilicata MSW production will be involved in quality variations which will be more remarkable than the quantity ones. Figure 5 shows the results of an estimation of the waste composition in the next 12 y.
A strong reduction of organic fraction (−7.6%), a light reduction of glass (−2.2%), a negligible variation of metals, a sensitive increase of papers and plastics (+8.8% and +8.6%, respectively) and a light increase of wood and textiles (+0.5%) will occur.
Table 3 reports the data relative to the percentage composition of the OS MSW. About half of the waste is smaller than 60 mm and less than 20% is composed by the fine fraction (<20 mm). The composition of the oversized fraction (>120 mm) largely depends on the high HV materials (plastic, paper and textiles), while the major part of the organic fraction is below 60 mm. Glass and inert matter have a homogeneous distribution.
|MSW fraction||Raw MSW||Sieve cut-off [mm]|
|Plastic and rubber||11.4||93.5||83.2||81.3||73.9||63.4|
|Wood, textile and leather||5.4||85.3||70.3||63.7||61.9||59.8|
|Glass and inert matter||6.6||89.7||67.1||50.3||32.4||15.8|
|Under-sieved (20 mm)||18.8||-||-||-||-||-|
Table 4 shows the HV of separated waste as a function of the sieve size.
|MSW fraction||Raw MSW||Sieve cut-off [mm]|
|Plastic and rubber||2,378.2||2,929.2||3,287.3||3,887.2||4,549.6||5,112.0||5,510.1|
|Wood, textile and leather||840.2||1,034.9||1,059.6||1,160.4||1,259.4||1,512.9||1,836.2|
|Glass and inert matter||-||-||-||-||-||-||-|
Considering the HV as a function of the MSW sieve cut-off, the trend is almost linear: the energy content of the fine fraction is about 64% of the oversized fraction (>120 mm).
3.2.1. Environmental Effects
Figure 6 shows the GHGs emissions for three proposed ISWM solutions.
As expected, the solution with direct landfilling (solution a) generates the highest emissions (e.g., biomethane). In areas where a low waste production occurs (such as Basilicata), the effect is more evident because of the long residence times of waste before the landfill closure and the biogas extraction network completion. The direct US landfilling coupled with OS incineration (solution b) generates more GHGs when the amount of burned MSW diminishes. The sieve cut-off influences also landfill volumes uses and energy recovery. In fact, smaller is the sieve cut-off (20–40 mm), the higher is the waste volume reduction; conversely, higher is the sieve cut-off (60–80 mm), the lower is the waste volume reduction and the higher is the energy recovery. The separation of the wet fraction, which is first aerobically stabilized in reactors and later disposed of in landfills (solution c) is the best solution, independently from the sieve cut-off; moreover, it allows to decrease the incineration unit size (theoretically, partly penalizing the potential energy recovery). We must also take into account that this phase will be gradually reduced by successively boosting of home composting.
3.2.2. Waste Incineration and Energy Recovery
According to an optimization procedure which considers a compromise between the environmental impact (GHG emissions) and the energy recovery, the sieve cut-off was set equal to 60 mm, corresponding to an HV equal to about 10.1 MJ kg−1 (Table 4).
For the gas-gas heat exchanger, the discharge is mGT = 1.3 mf (mf = 60 kg s−1) using a gas temperature in the turbine, T3 equal to 884 °C. The operating conditions of the gas turbine are: entry pressure of 9.1 kPa; pressure ratio (β) equal to 7.1. The entry temperature and pressure into the turbine are 60 bar and 440 °C, respectively. At the output, there is an optimum level for operation of the turbine, which is no lower than 0.9, and a temperature of approximately 100 °C. With a steam discharge equal to 8.4 kg s−1, the power produced by the alternator coupled with the gas turbine is 25.1 MW. The power developed by the steam turbine is 5.4 MW with a gradient that can be used to produce 30 °C hot water. The co-generated thermal power, Q, is 16.8 MW, which is transferred to a water flow, mw, of 200 kg s−1.
The second-principle yield (ηII), in the case of power generation only, is 0.47, while the first- and second-principle yields related to co-generation are 0.74 and 0.54, respectively. In the case of a demand for cold air (used for summer conditioning), ηI summer is 0.68. Therefore, the results show a co-generation second-principle yield lower than ηI because of the difference between the thermal power to the condenser and the electrical power, but higher than ηI in the case of electrical generation only. The major advantage associated with the co-generation respect to the power production must be compared to the higher costs of plant start-up and maintenance.
In the urban area of Potenza (the main town in Basilicata), the locations of the waste disposal, incineration and treatment plants aid the implementation of an interconnection system aimed at energy recovery. Thus, the best solution for the examined case is the integrated management of the energy sources, which entails (i) using the MSW combustible fraction; (ii) managing the landfill and (iii) stabilizing the wastewater treatment plant sludge. In fact, the thermal energy necessary for heating the anaerobic reactors as well as for evaporating percolates and digested sludge can be satisfied by cogeneration plant. Moreover, during summer, when cold is demanded for air-conditioning, it is possible to use an absorption refrigeration cycle, albeit such solution implies an increase in plant costs.
The rapid increase in volume and composition of MSW as a result of continuous economic growth, urbanization and industrialization is a problem for national and local governments, if they aim at ensuring an effective and sustainable management of waste. Solid waste incineration requires complex and sophisticated plants, whose running and installation costs are much higher than those of plants that work with traditional fuels. Moreover, energy recovery in fairly small-sized plants is affected by the high cost of the interventions.
The paper focuses on non-densely populated area where the production of urban waste is less than the urban ones. Considering the difficulties in waste collection due to geographic and demographic conditions, separated collection should be carried out only for complying with the regulations. The residual fraction should be sent to the incineration process for energy recovery, with positive environmental effects (in terms of GHGs emissions and landfill volumes) for the whole ISWM system.
Moreover, in low waste production area where the establishment of a unique MSW collection policy is difficult, the residual fraction quality is variable. Such issue can be solved with an appropriate pre-treatment process which improves the characteristics (e.g., heating value) of secondary fuel. The analysis of the obtained results in an Italian non-densely populated area demonstrates the potential of the co-generative incineration residual MSW for energy recovery after sieving, an effective and low cost pre-treatment process. Co-generative incineration is advantageous from an energetic point of view, especially considering the quality and the amount of the energy that can be obtained (power, heat and/or cold).
All these factors, including also the European regulations constraint and the low cost of secondary fuel which tends to increase its heating value, should be taken into account for a sustainable mid-term ISWM system planning in both developing and developed countries where the sustainable management of MSW cycle is penalized by the difficulties in source separated collection and the low flow of material recovery.
Conflicts of Interest
The authors declare no conflict of interest.
- United Nations—U.N. Environment Programme. Developing Integrated Solid Waste Management Plan; Training Manual; International Environmental Technology Centre: Osaka/Shiga, Japan, 2009; Volume 4. [Google Scholar]
- Cossu, R.; Masi, S. Re-thinking incentives and penalties: Economic aspects of waste management in Italy. Waste Manag. 2013, 33, 2541–2547. [Google Scholar] [CrossRef]
- Callegari, A.; Torretta, V.; Capodaglio, A.G. Preliminary trial application of biological desulfonation in pig farms’ anaerobic digesters. Environ. Eng. Manag. 2013, 12, 815–819. [Google Scholar]
- Rada, E.C.; Ragazzi, M.; Torretta, V. Laboratory-scale anaerobic sequencing batch reactor for treatment of stillage from fruit distillation. Water Sci. Technol. 2013, 67, 1068–1074. [Google Scholar] [CrossRef]
- Martinez, S.L.; Torretta, V.; Minguela, J.V.; Siñeriz, F.; Raboni, M.; Copelli, S.; Rada, E.C.; Ragazzi, M. Treatment of slaughterhouse wastewaters using anaerobic filters. Environ. Technol. 2013. [Google Scholar] [CrossRef]
- Torretta, V.; Rada, E.C.; Istrate, I.A.; Ragazzi, M. Poultry manure gasification and its energy yield. UPB-Sci. Bull. Ser. D 2013, 75, 231–238. [Google Scholar]
- Vaccari, M.; Torretta, V.; Collivignarelli, C. Effect of improving environmental sustainability in developing countries by upgrading solid waste management techniques: A case study. Sustainability 2012, 4, 2852–2861. [Google Scholar] [CrossRef]
- Hartmann, H.; Ahring, B.K. Anaerobic digestion of the organic fraction of municipal solid waste: Influence of co-digestion with manure. Water Res. 2005, 39, 1543–1552. [Google Scholar] [CrossRef]
- Chaerul, M.; Tnaka, M. A system dynamics approach for hospital waste management. Waste Manag. 2008, 28, 442–449. [Google Scholar] [CrossRef]
- Birpmar, M.E.; Bilgili, M.S.; Erdoğan, T. Medical waste management in Turkey: A case study of Istanbul. Waste Manag. 2009, 29, 445–448. [Google Scholar] [CrossRef]
- Abdulla, F.; Abu Qdais, H.; Rabi, A. Site investigation on medical waste management practices in northern Jordan. Waste Manag. 2008, 28, 450–458. [Google Scholar] [CrossRef]
- Mancini, G.; Tamma, R.; Viotti, P. Thermal process of fluff: Preliminary tests on a full-scale treatment plant. Waste Manag. 2010, 30, 1670–1682. [Google Scholar] [CrossRef]
- Torretta, V.; Istrate, I.; Rada, E.C.; Ragazzi, M. Management of waste electrical and electronic equipment in two EU countries: A comparison. Waste Manag. 2013, 33, 117–122. [Google Scholar] [CrossRef]
- Di Mauro, C.; Bouchon, S.; Torretta, V. Industrial risk in the Lombardy Region (Italy): What people perceive and what are the gaps to improve the risk communication and the partecipatory processes. Chem. Eng. Trans. 2012, 26, 297–302. [Google Scholar]
- Morris, M.W.; Su, S.K. Social psychological obstacles in environmental conflict resolution. Am. Behav. Sci. 1999, 42, 1322–1349. [Google Scholar] [CrossRef]
- European Council. Directive 91/156/EEC Amending Directive 75/442/EEC on Waste; Official Journal L 078, 26/03/1991 P. 0032 – 0037; EEC: Brussels, Belgium, 1991. [Google Scholar]
- European Council. Directive 91/689/EEC on Hazardous Waste; Official Journal L 377, 31/12/1991 P. 0020 – 0027; EEC: Brussels, Belgium, 1991. [Google Scholar]
- European Parliament and Council. Directive 94/62/EC on Packaging and Packaging Waste; Official Journal L 365, 31/12/1994, P. 0010–0023; EC: Brussels, Belgium, 1994. [Google Scholar]
- European Parliament and Council. Directive 2000/76/EC on the Incineration of Waste; Official Journal L 332, 28/12/2000, P. 0091; EC: Brussels, Belgium, 2000. [Google Scholar]
- Italian Parliament. Decreto Legislativo 5 febbraio 1997, n. 22 “Attuazione delle direttive 91/156/CEE sui rifiuti, 91/689/CEE sui rifiuti pericolosi e 94/62/CE sugli imballaggi e sui rifiuti di imballaggio”. Available online: http://www.parlamento.it/parlam/leggi/deleghe/97022dl.htm (accessed on 2 May 2013).
- Italian Parliament. Decreto Legislativo 3 aprile 2006, n. 152 “Norme in materia ambientale”. Available online: http://www.camera.it/parlam/leggi/deleghe/06152dl.htm (accessed on 2 May 2013).
- Eriksson, O.; Carlsson, R.M.; Frostell, B.; Björklund, A.; Assefa, G.; Sundquist, J.-O.; Granath, J.; Baky, A.; Thyselius, L. Municipal solid waste management from a systems perspective. J. Clean. Prod. 2005, 13, 241–252. [Google Scholar] [CrossRef]
- Tascione, V.; Raggi, A. Identification and selection of alternative scenarios in LCA studies of integrated waste management systems: A review of main issues and perspectives. Sustainability 2012, 4, 2430–2442. [Google Scholar] [CrossRef]
- Bovea, M.D.; Ibáñez-Forés, V.; Gallardo, A.; Colomer-Mendoza, F.J. Environmental assessment of alternative municipal solid waste management strategies: A Spanish case study. Waste Manag. 2010, 30, 2383–2395. [Google Scholar] [CrossRef]
- De Feo, G.; Malvano, C. The use of LCA in selecting the best MSW management system. Waste Manag. 2009, 29, 1901–1915. [Google Scholar] [CrossRef]
- Iriarte, A.; Gabarrel, X.; Rieradevall, J. LCA of selective waste collection systems in dense urban areas. Waste Manag. 2009, 29, 903–914. [Google Scholar] [CrossRef]
- Emery, A.; Davies, A.; Griffiths, A.; Williams, K. Environmental and economic modelling: A case study of municipal solid waste management scenarios in Wales. Resour. Conserv. Recycl. 2007, 49, 244–263. [Google Scholar] [CrossRef]
- Chang, Y.H.; Chang, N.B. Compatibility analysis of material and energy recovery in a regional solid waste management system. J. Air Waste Manag. Assoc. 2003, 53, 32–40. [Google Scholar] [CrossRef]
- Di Maria, F.; Micale, C. Impact of source segregation intensity of solid waste on fuel consumption and collection costs. Waste Manag. 2013, 33, 2170–2176. [Google Scholar] [CrossRef]
- Nguyen, T.T.T.; Wilson, B.G. Fuel consumption estimation for kerbside municipal solid waste (MSW) collection activities. Waste Manag. Res. 2010, 28, 289–297. [Google Scholar] [CrossRef]
- European Commission. Eurostat Database. Available online: http://epp.eurostat.ec.europa.eu/portal/page/portal/statistics/search_database (accessed on 1 December 2013).
- Tchobanoglous, G.; Kreith, F. Handbook of Solid Waste Management; Mc-Graw-Hill: New York, NY, USA, 2002. [Google Scholar]
- Murphy, J.D.; McKeogh, E. Technical, economic and environmental analysis of energy production from municipal solid waste. Renew. Energy 2004, 29, 1043–1057. [Google Scholar] [CrossRef]
- Rimaitytė, I.; Denafas, G.; Martuzevicius, D.; Kavaliauskas, A. Energy and environmental indicators of municipal solid waste incineration: Toward selection of an optimal waste management system. Pol. J. Environ. Stud. 2010, 19, 989–998. [Google Scholar]
- Italian Institute of Statistics (ISTAT). Maps and Census Data. (in Italian). Available online: http://www.istat.it/it/strumenti/cartografia (accessed on 23 April 2013).
- Institute for the Environmental Protection and Research—ISPRA. Rapporto rifiuti urbani (Municipal Waste Report); ISRRA: Rome, Italy, 2012. [Google Scholar]
- Regione Basilicata. Piano regionale gestione rifiuti, Potenza, Italy. Available online: http://www.regione.basilicata.it/giunta/files/docs/DOCUMENT_FILE_242375.pdf (accessed on 20 April 2013).
- Consonni, S.; Viganò, F. Material and energy recovery in integrated waste management systems: The potential for energy recovery. Waste Manag. 2011, 31, 2074–2084. [Google Scholar] [CrossRef]
- Valkenburg, C.; Gerber, M.A.; Walton, C.W.; Jones, S.B.; Thompson, B.L.; Stevens, D.J. Municipal Solid Waste (MSW) to Liquid Fuels Synthesis, Volume 1: Availability of Feedstock and Technology; U.S. Deptartment of Energy: Washington, DC, USA, 2008. [Google Scholar]
- Cosmi, C.; Cuomo, V.; Macchiato, M.; Mangiamele, L.; Masi, S.; Salvia, M. Waste management modeling by MARKAL model: A case study for Basilicata Region. Environ. Model. Assess. 2000, 5, 19–27. [Google Scholar] [CrossRef]
- Cosmi, C.; Mancini, I.; Mangiamele, L.; Masi, S.; Salvia, M.; Macchiato, M. The management of urban waste at regional scale: The state of the art and its strategic evolution—Case study Basilicata Region (Southern Italy). Fresenius Environ. Bull. 2001, 10, 131–138. [Google Scholar]
- Çengel, Y.A. Introduction to Thermodynamics and Heat Transfer; McGraw-Hill: New York, NY, USA, 2007. [Google Scholar]
- Environmental Protection Agency—Ireland. Municipal Solid Waste—Pre-treatment & Residuals Management; IR-EPA: Wexford, Ireland, 2009. [Google Scholar]
- Sue, D.C.; Chuang, C.C. Engineering design and energy analyses for combustion gas turbine based power generation system. Energy 2004, 29, 1183–1205. [Google Scholar] [CrossRef]
- Roher, A. Comparison of combined heat and power generation plants. ABB Review 1996, 3, 24–32. [Google Scholar]
- Lombardi, F.; Lategano, E.; Cordiner, S.; Torretta, V. Waste incineration in rotary kilns: A new simulation combustion’s tool to support design and technical change. Waste Manag. Res. 2013, 31, 739–750. [Google Scholar] [CrossRef]
© 2013 by the authors; licensee MDPI, Basel, Switzerland. This article is an open access article distributed under the terms and conditions of the Creative Commons Attribution license (http://creativecommons.org/licenses/by/3.0/).