Environmental Assessment of Solid Recovered Fuel Production from Screening Waste Using a Life Cycle Assessment Approach
Abstract
:1. Introduction
2. Materials and Methods
2.1. Goal and Scope Definition
2.2. Proposed Scenarios
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- Scenario 1 (S1): Disposal in landfill.
- -
- Scenario 2 (S2): Production of non-densified SRF with solar drying.
- -
- Scenario 3 (S3): Production of non-densified SRF with thermal drying.
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- Scenario 4 (S4): Production of densified SRF with solar drying.
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- Scenario 5 (S5): Production of densified SRF with thermal drying.
2.3. Inventory Analysis
- -
- Transport: only road transport to landfill was considered, whose environmental impact is fundamental to the LCA methodology. The distance from the waste collection point (Biofactoría Sur of Granada) to the destination landfill is 19.7 km. For the scenarios with SRF production, all the screening waste treatment would be carried out at the Biofactoría per se, so transport did not need to be considered in such cases.
- -
- Landfilling: it was not possible to obtain primary data on the emissions produced from the current disposal of screening waste in the specific landfill for Biofactoría Sur. Based on this, the authors have used secondary data for these emissions, obtained for similar landfills in Spain, generally for the disposal of organic municipal solid waste.
- -
- Drying: the objective of this process is to achieve approximately 15% moisture content in the screening waste, a percentage that some authors regard as ‘dry residue’, which would also meet the moisture requirements for use as fuel in some thermochemical processes [22]. This stage was defined for two drying processes to compare their potential environmental impact. Firstly, solar drying or bio-drying was carried out in a greenhouse containing a scarification roller and a system for moving air in and out [45]. Secondly, which is more established in drying processes, trommel drying was implemented, which is more efficient for waste with a large amount of water [38].
- -
- Shredding: triturating the already dry screening waste is a complicated task due to the high percentage of sanitary textiles and their resistance to grinding. The process aims to reduce and homogenise the particle size of the residue. Once this stage is completed, the residue becomes SRF without densification.
- -
- Densification: the output stream of the previous process, non-densified SRF, is the input stream of this process. This stage involves the conditioning of the SRF as pellets through compaction.
2.4. Life Cycle Impact Assessment
3. Results and Discussion
4. Conclusions
Author Contributions
Funding
Data Availability Statement
Acknowledgments
Conflicts of Interest
References
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Waste Fractions | Description | Volume from Total Solids (%) | Process Unit in SimaPro | Amount [kg] * |
---|---|---|---|---|
Sanitary textiles | Tampons, sanitary towels, wipes, etc. | 52.10 | Sanitary textiles | 0.1183 |
Paper and cardboard | Newspapers, brown corrugated cardboard, package paper rolls, office paper | 11.80 | Waste paperboard, sorted (GLO) market for cut-off, S | 0.0268 |
Organic | Leaves, flowers, plant parts, food scraps, etc. | 5.50 | Wood chips, wet, measured as dry mass (Europe without Switzerland) market for cut-off, S | 0.0125 |
Plastics | Plastic film, bottles, rigid plastic, packaging, condoms, wrapping and bags | 5.00 | Polystyrene, general purpose (GLO) market for cut-off, S | 0.0113 |
Other | Fractions that are very costly to separate, including inert debris, hair, organic matter and fine particulates (<20 mm) | 25.90 | Compost (GLO) market for cut-off, S + sand (RoW), market for sand cut-off, S | 0.0588 |
Inputs | Database Process Unit | Unit | Value | Notes |
---|---|---|---|---|
Transport | ||||
Materials | Raw screening waste | kg | 1 | Moisture of 77.3% |
Processes | Transport, truck < 10 t, EURO3, 20% LF, empty return/GLO energy | tkm | 0.039 | |
Landfill | ||||
Materials | Raw screening waste | kg | 1 | Moisture of 77.3% |
Processes | Screening from WWTP (waste scenario). Treatment of municipal solid waste, landfill, cut-off, S | p | 1 | |
Solar drying | ||||
Materials | Raw screening waste | kg | 1 | Moisture of 77.3% |
Processes | Greenhouse for solar drying | p | 1 | To evaporate 0.623 kg of wastewater |
Electricity | Electricity, high voltage {ES}|market for|cut-off, S | kWh | 0.040 | |
Thermal drying | ||||
Materials | Raw screening waste | kg | 1 | Moisture of 77.3% |
Processes | Trommel drying | p | 1 | To evaporate 0.623 kg of wastewater |
Electricity | Electricity, high voltage {ES}| market for|cut-off, S | kWh | 0.560 | |
Trituration | ||||
Materials | Dry screening waste | kg | 0.377 | Moisture of 15% |
Processes | Chipper, stationary, electric {GLO}| chipper production, stationary, electric|cut-off, S | p | 1 | A water loss of 0.3% is considered |
Electricity | Electricity, high voltage {ES}| market for|cut-off, S | kWh | 0.014 | |
Densification | ||||
Materials | Non-densified SRF | kg | 0.376 | |
Processes | Pelletiser [45] | p | 1 | A water loss of 3% is considered |
Electricity | Electricity, high voltage {ES}| market for|cut-off, S | kWh | 0.001 | |
Diesel | Diesel {Europe without Switzerland}|market for|cut-off, S | kg | 0.004 |
Impact Category | Unit | S1 | S2 | S3 | S4 | S5 |
---|---|---|---|---|---|---|
ADP | kg Sbeq | 4.40 × 10−6 | 1.33 × 10−5 | 35 × 10−5 | 1.93 × 10−5 | 1.95 × 10−5 |
% | 6.3 | 19.1 | 19.3 | 27.5 | 27.8 | |
ADP (fossil) | MJ | 29.0 | 28.8 | 30.6 | 41.7 | 43.6 |
% | 16.7 | 16.6 | 17.6 | 24.0 | 25.1 | |
GWP100a | kg CO2eq | 2.41 | 1.27 | 1.43 | 1.83 | 1.99 |
% | 26.9 | 14.2 | 16.0 | 20.5 | 22.3 | |
ODP | kg CFC-11eq | 5.05 × 10−7 | 1.56 × 10−6 | 1.56 × 10−6 | 2.25 × 10−6 | 2.26 × 10−6 |
% | 6.2 | 19.1 | 19.2 | 27.7 | 27.8 | |
HTP | kg 1.4-DBeq | 5.19 × 10−1 | 6.43 × 10−1 | 7.06 × 10−1 | 9.28 × 10−1 | 9.90 × 10−1 |
% | 13.7 | 17.0 | 18.6 | 24.5 | 26.2 | |
FAETP | kg 1.4-DBeq | 2.11 | 4.87 × 10−1 | 5.42 × 10−1 | 7.02 × 10−1 | 7.56 × 10−1 |
% | 45.9 | 10.6 | 11.8 | 15.3 | 16.5 | |
MAETP | kg 1.4-DBeq | 1.40 × 103 | 1.35 × 103 | 1.60 × 103 | 1.94 × 103 | 2.19 × 103 |
% | 16.5 | 15.9 | 18.9 | 22.9 | 25.8 | |
TETP | kg 1.4-DBeq | 3.18 × 10−3 | 1.61 × 10−3 | 1.81 × 10−3 | 2.32 × 10−3 | 2.52 × 10−3 |
% | 27.8 | 14.1 | 15.8 | 20.3 | 22.0 | |
PO | kg C2H4eq | 6.30 × 10−4 | 3.02 × 10−4 | 3.45 × 10−4 | 4.36 × 10−4 | 4.79 × 10−4 |
% | 28.7 | 13.8 | 15.7 | 19.9 | 21.8 | |
AP | kg SO2eq | 9.94 × 10−3 | 4.65 × 10−3 | 5.82 × 10−3 | 6.69 × 10−3 | 7.86 × 10−3 |
% | 28.4 | 13.3 | 16.6 | 19.1 | 22.5 | |
EP | kg PO4eq | 4.93 × 10−3 | 1.26 × 10−3 | 1.52 × 10−3 | 1.80 × 10−3 | 2.07 × 10−3 |
% | 42.6 | 10.9 | 13.1 | 15.6 | 17.8 |
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De la Torre Bayo, J.J.; Zamorano, M.; Torres-Rojo, J.C.; Pennellini, S.; Martín-Pascual, J.; Bonoli, A. Environmental Assessment of Solid Recovered Fuel Production from Screening Waste Using a Life Cycle Assessment Approach. Processes 2024, 12, 1814. https://doi.org/10.3390/pr12091814
De la Torre Bayo JJ, Zamorano M, Torres-Rojo JC, Pennellini S, Martín-Pascual J, Bonoli A. Environmental Assessment of Solid Recovered Fuel Production from Screening Waste Using a Life Cycle Assessment Approach. Processes. 2024; 12(9):1814. https://doi.org/10.3390/pr12091814
Chicago/Turabian StyleDe la Torre Bayo, Juan Jesús, Montserrat Zamorano, Juan C. Torres-Rojo, Sara Pennellini, Jaime Martín-Pascual, and Alessandra Bonoli. 2024. "Environmental Assessment of Solid Recovered Fuel Production from Screening Waste Using a Life Cycle Assessment Approach" Processes 12, no. 9: 1814. https://doi.org/10.3390/pr12091814