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Article

Assessing the Environmental Performance of Municipal Solid Waste Collection: A New Predictive LCA Model

1
UNESCO Chair in Life Cycle and Climate Change, Escola Superior de Comerç Internacional (UPF), Passeig Pujades, 1, 08003 Barcelona, Spain
2
School of Engineering, Computing and Mathematics, Oxford Brookes University, Wheatley Campus, Wheatley OX33 1HX, UK
3
Centre for the Research and Technology of Agro-Environmental and Biological Sciences, University of Trás-os-Montes and Alto Douro, Quinta de Prados, 5000-801 Vila Real, Portugal
4
Ecoembalajes España, S.A., Calle de Cardenal Marcelo Spínola 14/2ª planta, 28016 Madrid, Spain
5
Circular Economy and Waste Advisor, 10 Azagador, Las Rozas de Madrid, 28232 Madrid, Spain
*
Author to whom correspondence should be addressed.
Sustainability 2021, 13(11), 5810; https://doi.org/10.3390/su13115810
Received: 22 April 2021 / Revised: 18 May 2021 / Accepted: 20 May 2021 / Published: 21 May 2021
(This article belongs to the Special Issue Municipal Solid Waste Management)

Abstract

:
Most existing life cycle assessment models of waste management have so far underplayed the importance of the waste collection phase, addressing it only in a simplified fashion, either by requesting the total amount of fuel used as a direct user input or by calculating it based on a set of input parameters and fixed diesel consumption factors. However, if the main purpose of the study is to improve the efficiency of the collection system itself, a more detailed analysis of the collection phase is required, avoiding oversimplified and potentially misleading conclusions. The new LCA collection model presented here relies on a large number of parameters (number and type of containers, collection frequency, distances for the various legs of transport, etc.) and allows the detailed predictive analysis of alternative collection scenarios. The results of applying this newly developed model to a number of experimental case studies in Portugal are analyzed, discussed, and compared to those produced by a selection of pre-existing, more simplified models such as ORWARE and MSW-DST. The new model is confirmed as being the most accurate and, importantly, as the only one capable of predicting the consequences of a range of possible changes in the collection parameters.

1. Introduction

LCA was originally developed to analyze the environmental performance of product systems; however, since the end of the 1990s, this methodology has also been used for the analysis of waste management systems [1]. Since then, hundreds of scientific papers on this topic have been published. Proof of this sharp increase all over the world is the review of 222 LCA studies comparing waste management systems before 2013 performed by Laurent et al. in 2014 [2]; the review of 153 worldwide studies after 2013 performed by Khandelwal et al. in 2019 [3]; and the even more recent reviews of 79 papers performed by Iqbal et al. in 2020 [4] and of 45 studies by Zhang et al. in 2021 [5], both of which included selected case studies from developing and developed regions. Until 2013, the majority of studies were performed in Europe, whereas from this date on, there has been a remarkable increase in the use of LCA in China and also a progressive extension to other low-income or less developed countries such as India, Brazil, or Pakistan.
In all these studies, LCA was used to compare different alternatives for the treatment of a specific waste flow such as paper [6,7,8,9], plastic [10,11,12], or organic waste [13,14,15]; to compare or improve different technologies [16,17,18,19,20]; and also to compare more complex systems such as complete integrated waste management systems, including all waste fractions [21,22,23,24,25,26,27,28,29,30,31,32,33]. The benefit of using LCA in this context is that it helps to expand the scope of the analysis and to obtain a complete view of the entire system, including all processes and associated environmental impacts. This approach can avoid the unintentional shifting of environmental loads between different stages of the waste management system, geographic areas, environmental compartments (air, land, and water), or impact categories (e.g., global warming, acidification, etc.).
In this context, LCA has gained importance in recent years as a tool to assist decision making for waste management policy and planning in Europe [34,35]. Although some authors performed their studies using conventional LCA software and databases such as Simapro and Ecoinvent [14,28], the methodological development of LCA for waste management has gone hand in hand with the development of models and specific software tools to facilitate its implementation by non-LCA experts. These models have been developed almost independently, and mainly in Europe and North America, from the mid-1990s onwards by a wide range of universities, consultancy firms, and environmental protection agencies (Table 1).
All these software packages have in common the inclusion of specific datasets for a wide range of unit processes (waste collection, sorting, recycling, incineration, landfilling, composting, or anaerobic digestion), and the possibility for users to build their own waste management systems by combining these unit processes and specifying waste generation, waste composition, and/or recovery rates to arrive at specific results for their system(s) of interest.
In-depth reviews of the existing models were carried out by Björklund et al. [57] and Gentil et al. [56]. Both studies featured comparisons based on methodological issues, input parameters, and modeling assumptions, and concluded that there are substantial differences in the models, often linked to the date of development and the level of knowledge at that time. Along the same lines, other authors evaluated the same management systems or waste management processes using different models to check if the results were comparable. Examples of such comparative work are those by Hansen and Christensen [58], comparing organic waste treatments; Winkler and Bilitewski [59], comparing the entire management system of the city of Dresden in Germany; and Rimaityté et al. [60], comparing the outcomes of waste incineration using different models and also vs. experimental data.
However, no comparative meta-analyses of the results of applying different LCA models to the waste collection phase were found in the literature. This is probably due to the fact that, while this latter phase of the management system accounts for a major part of the total costs of modern waste management systems [61], several LCAs have shown that its overall effect in terms of energy demand and emissions of CO2, SO2, and NOx remains comparatively small, provided that the collection and transport systems are reasonably efficient [62,63,64,65]. In fact, the recent review by Iqbal et al. of the use of LCA for WMS revealed that about 16% of the studies excluded waste collection and transport altogether, assuming that their contributions would be insignificant compared to the rest of waste management chain [4]. The general validity of these findings in relative terms, i.e., that the waste collection stage is the smallest contributor to the overall environmental impacts of the entire waste management chain, is not questioned. However, in many cases, waste collection is in fact the one process that can be most directly controlled and optimized by actors such as local municipalities and waste management companies, and its impacts can still be rather large in absolute terms. Therefore, the lack of a detailed predictive tool capable of accurately estimating the environmental consequences of a range of specific collection alternatives represents a significant gap in the existing LCA knowledge base.
The drive for implementing a source-separated collection system for different waste fractions rests on the assumption that the amount and quality of the waste collected in such a way are sufficient to overcompensate for the additional environmental burdens entailed by the more complex collection system (thanks to the environmental credits arising from the recovered materials and/or energy), or, in other words, that the collection and transport systems are reasonably efficient. The national implementation of the Directive 2008/98/EC of the European Parliament and the Council on waste [66] led many countries to introduce a legal obligation of establishing a source-separated collection for plastics, glass, paper and cardboard, metals, and also organic waste. However, in countries like Spain or Portugal, where many of the municipalities are very small (under 5000 inhabitants) and scattered around the territory, whether source-separated collection is really environmentally sound and effective in all cases remains to be carefully assessed.
Some authors have questioned the premise of collection efficiency and pointed out that this stage of the waste management system can have a major influence on the overall outcome, depending on how it is implemented. For instance, Klang [67] states that in rural and sparsely populated areas of Sweden, it is “more difficult to transform their waste systems in a more sustainable direction”, due to small waste volumes, long collection routes, and distant treatment facilities. Along the same lines, Tanskanen and Kaila [68] pointed out that the increasing complexity of the collection systems in terms of the amount of different waste fractions collected separately, and the associated transport and fuel consumption, may increase the relevance of this stage. Salhofer and colleagues [69] demonstrated how transport distances may affect the environmental benefit of recycling a range of waste flows (refrigerators, waste paper, polyethylene films, and expanded polystyrene). In the same way, Aryan et al. in India [70] and Ahamed et al. in Singapore [14] demonstrated that the collection and transport of PET and PE in the former and food waste in the latter may have a high contribution to the global warming potential of the systems, ranging from 23% for food waste up to 40% for PET, due to the large distances to recycling facilities. All this calls for a better focus on the collection phase to assess whether (or the extent to which) the additional environmental burdens associated to the source-separated collection of municipal solid waste are in fact offset by the attainable higher recovery rates of materials and energy from waste.
The aim of this paper is thus two-fold. Firstly, it provides a careful review of existing models for the LCA of waste management systems and looks at whether or not they do a satisfactory job of estimating the fuel consumption and the associated impacts in the waste collection phase. Secondly, it introduces a new, more complete and detailed model to predict the environmental performance of the waste collection phase, in which changes in the operational parameters of the system (such as, e.g., the number or volume of waste containers, changes in the distances between containers or between the collection area and unloading site, etc.) have a direct effect on the modeled fuel consumption and emission rates.

2. Review of Existing Models

When dealing with the environmental performance of the waste collection phase, three different levels of complexity can be found among the LCA software packages listed in Table 1. The first level comprises those models that require that the user input the total amount of fuel (e.g., diesel) consumed directly (such is the case of IWM-2), and then apply fixed emission factors associated to the combustion of this fuel. Second level models require the input of fuel consumption (or efficiency) rates (e.g., in terms of km traveled per liter of diesel, liters of diesel consumed per ton of collected waste, or liters of diesel consumed per hour of service) and the input of the amount of waste and/or km traveled and/or the overall collection time in order to calculate the total fuel consumption. Then, corresponding emission factors are also applied. Within this second type of model, a distinction can be made between models in which the user is required to specify their own consumption factors (for instance, IWM-Canada and EASEWASTE/EASETECH), and others in which default values are provided, which may be changed by the user either manually or by selecting different truck types from a database (WRATE and LCA-IWM). Third level models are those in which the distances or time spent in the collection stage are not directly entered by the user but instead calculated by means of a set of operational parameters like travel speed, distances between individual collection points along the route, time spent in different operations, etc. Such km or hours spent are then multiplied by fixed consumption factors (L/km, L/h, or L/(t.km)), either introduced by the user or provided by default (as in MSW-DST and ORWARE). Like in the previous cases, emission factors are then applied to convert the diesel consumption into airborne emissions in order to evaluate the environmental impact of the collection stage.
It is worth noting that, in the end, existing simplified models (both level 2 and ‘level 3′ types) are still similarly limited in assuming a straightforward direct correlation between the distance traveled, waste collected or time spent collecting (in the case of MSW-DST), and the fuel consumed. These models may be regarded as arguably sufficient only for a quick estimate of the environmental impacts of the collection phase within the framework of a broader analysis of a complete waste management system, especially when the average collection performance (in terms of L (fuel)/t (waste), L (fuel)/km, or total fuel consumption) is already known. However, they fail to provide a sufficient level of detail if the focus of the analysis is on the optimization of the waste collection system itself. Questions like the following cannot be answered using such simplified models if no real data are available: “what if rear-loading trucks were replaced by side-loading trucks, using fewer larger containers?” or “what if the number of containers were reduced and the collection frequency were doubled?”. In order to answer these types of questions, more sophisticated models are needed, which must be able to predict the ensuing changes in the performance of the waste collection system. The original model presented in this paper is aimed squarely at filling this knowledge gap.

3. Materials and Methods

The steps followed in order to achieve the aims of this research are summarized in Figure 1. The materials and methods used are described in the following subsections.

3.1. Selection of Pre-Existing Models for Review and Comparison

The scope of this review and comparison will be restricted to level 3 models, plus the stock model for waste collection trucks included in Ecoinvent, since the latter is arguably the most widely-used life cycle inventory database used by LCA practitioners. The selected models are described below.
  • ORWARE: This model is based on the calculation of fuel consumption and emissions for waste collection trucks, considering two different situations: while collecting waste and while traveling from the collection area to the unloading site. Data on average load, average speed, etc. are used as input parameters. Data on energy consumption (MJ/(t.km)) were obtained from average data provided by the Uppsala Public Service Work in 1994 and emissions from a simulation of an average bus tour in an urban area with many stop-and-go cycles and a rather low average speed. The author explicitly mentions that this model is only valid for the collection of waste in urban areas. Data for energy consumption (converted to the international system of units (SI)) are shown in Table 2. A complete description can be found in [71].
  • MSW-DST: This model includes a set of equations to calculate the time required for the individual activities of the collection vehicles in a typical working day (driving to the collection area, driving in stop-and-go cycles, and idling at the stops). These times are then used to calculate the associated fuel consumption, based on corresponding fixed consumption factors (gallons per mile and gallons per hour)—see Table 2 for the values converted to SI. A complete description of the model and equations can be found in [72].
  • Ecoinvent dataset for collection trucks (”CH: transport, municipal waste collection, lorry 21 t”): This dataset is based on five case studies for German and Swiss municipalities, from which an average consumption rate of 4 L/t was obtained. The (fixed) transportation distance was estimated from the standard transport distance to municipal solid waste incineration plants in Ecoinvent, i.e., 10 km. From these values, an average fuel consumption factor expressed as L/(t·km) was derived—also included in Table 2. For further details, the reader is referred to Doka [73].

3.2. Experimental Data Collection

Weekly experimental data from 14 different curb-side collection routes were gathered in 2012 in Portugal (Lisbon and surrounding areas). These routes refer to the source-separated collection of different waste fractions, namely: mixed municipal solid waste (MSW), light packaging waste (LPW), paper and cardboard (P), and glass (G). All the routes correspond to more residential areas, except routes (LP2 and P2) that correspond to more commercial areas. For all routes, specific data were gathered, including total amount of waste collected, number of containers, distances between different parts of the collection route, and total fuel (diesel) consumption.

3.3. Development of a New Model: The FENIX Model

Within the EU Life+ project “FENIX”, a new predictive LCA model for the assessment of the environmental performance of the waste collection stage (hereinafter, the FENIX model) was developed. In this model, the collection stage includes both the effective collection leg of the route (within urban areas) as well as other distances traveled by the collection trucks, from the moment they leave the parking until they return to it (the latter distances collectively referred to as “transportation” in the model) (see Figure 2).
The development started by modifying a pre-existing model for a conventional transport truck to factor in the additional fuel consumption due to the specific stop-and-go drive cycles and other intrinsic characteristics of the waste collection truck, as well as to lifting the waste containers and compacting the waste. Finally, a detailed model for the calculation of the needed input parameters to run the modified collection truck model was developed based on a set of operational parameters and limiting factors.

3.3.1. Starting Point: A Conventional Commercial Truck

The FENIX model is based on the parameterized truck models developed by Sphera and available in the built-in database of the GaBi LCA software package, as well as in the (now discontinued) European Reference Life Cycle Database (ELCD). Essentially, those models calculate variable fuel (diesel) consumption and emission factors (CO2, CO, N2O, NH3, NMVOC, CH4, NOx, SO2, Toluene, Xylene, and PM) in terms of mass units per (kg·km) of transport. The fuel consumption factors are computed according to Equation (1):
D i e s e l c f = j = 1 3 [ α j × ( A j + ( B j A j ) × U r ) / ( P l × U r ) ]
where Dieselcf is the diesel consumption factor (kg(diesel)/(kg·km)); j is the type of road (1 = urban; 2 = extra-urban; 3 = motorway); αj is the share of km traveled in each type of road (-); Aj is the diesel consumption of the empty truck, depending on the type of road (speed and driving conditions) (kg(diesel)/km); Bj is the diesel consumption of the full truck, depending on the type of road (speed and driving conditions) (kg(diesel)/km); Pl is the maximum payload capacity of the truck (kg); and Ur is the utilization (fill) ratio of the truck by mass (-).
Then, the total amount of diesel consumed to transport goods is calculated as detailed in Equation (2):
D i e s e l   =   D i e s e l c f   ×   L o a d   ×   D T
where DieselT is the total diesel consumption (kg(diesel)); Load refers to the total transported mass (kg); and DT refers to the total distance traveled to transport the load (km).
In such base models, Equations (1) and (2) are formulated in the same way for calculating the emissions of CO2, CO, NMVOC, CH4, NOx, Toluene, Xylene, and PM. The only difference is that factors Aj and Bj refer to the correspondent mass of substance emitted per km. The remaining emission factors, namely those for N2O, NH3, and SO2 are calculated according to Equations (3)–(5), respectively.
N 2 O e f = j = 1 3 [ α j × E j / ( P l × U r ) ]
N H 3 e f = E / ( P l × U r )
S O 2 e f = P P M × 2 × D i e s e l c f
where Ej is the emission factor, depending on the type of road (speed and driving conditions) (mg/km); E is the average emission factor (mg/km); PPM is the proportion of sulfur in diesel (ppm), and 2 is the ratio of the molecular mass of SO2 to that of S (kg(SO2)/kg(S)).

3.3.2. Adaptation of the Conventional Truck to Waste Collection Vehicles

Waste collection vehicles differ from conventional trucks in their performance because they have different intrinsic characteristics. First of all, waste collection vehicles continuously carry the additional load of the heavy box and equipment used to collect and compact the waste. Moreover, their operation entails more stop-and-go cycles in comparison to conventional trucks, since they have to stop and start again every time they collect the waste at each collection point. Additionally, while the trucks are stationary, the engines still operate at high revolutions per minute (RPMs) in order to lift the waste containers from the curb and compress their content. Another important difference is related to the utilization ratio (Ur) of the truck. Whereas the Ur of a conventional truck would remain constant, from the loading site all the way to the unloading site, the same parameter for a waste collection truck varies along the collection route (increasing as more and more waste is collected). For all these reasons, it was necessary to modify the basic truck model described above in order to incorporate the additional diesel consumption and related emissions.
The additional consumption due to the heavy box and equipment, the additional stop-and-go cycles, and the variable utilization ratio were considered by including a correction parameter (βj), which is the ratio of consumption/emission factor of a waste collection truck to that of a conventional one (Equation (6)).
β j = D i e s e l c f / D i e s e l c f
where Dieselcf is the diesel consumption factor (kg(diesel)/(kg·km) of the collection truck.
D i e s e l c f = j = 1 2 [ α j × ( A j + ( B j A j ) × U r ) / ( P l × U r ) ]
where αj is the share of km traveled in each leg of the collection route (respectively, j = 1 for transport and j = 2 for effective collection), Aj is the diesel consumption of the empty collection truck (including the box) in each leg [kg(diesel/)km]; Bj is the diesel consumption of the full collection truck (including the box) in each leg, also depending on the number of additional stops per trip (kg(diesel)/km); Ur is the utilization (fill) ratio of the collection truck by mass (-); and P l = ( P l W b o x ) ) is the maximum effective payload capacity of the truck (discounting the weight of the box) (kg); and Wbox is the weight of the box used to store and compact the waste (kg).
The share of km travelled during the effective collection and the transportation legs or the route (αj) and the total distance per collection trip (DT) are calculated as detailed in Equations (8)–(11).
α 2 = 1 α 1
α 1 = ( D T D 2 ) /   D T
D T = [ D 1 + D 2 + ( N 1 ) × 2 D 3 + D 3 + D 4 ] /   N
D 2 = ( C 1 ) × D c
where, again α2 is the share of km travelled during the effective collection (-); α1 is the share of km traveled the rest of the collection route (-); C is the number of containers (or collection stops) (-); D1 is the distance between the parking lot and the collection route (km); D2 is the total distance while collecting waste (effective collection) (km); D3 is the distance from the collection area to the unloading site (km); D4 is the distance between the unloading site and the parking lot (km); and Dc is the average distance in between individual containers or collection stops (km).
All calculations were carried out in an Excel worksheet. The number of trips per truck (N) was calculated taking into account the following limiting factors in an iterative way: (1) the maximum number of containers in the collection route, (2) the maximum volume or weight capacity of the truck, and (3) the maximum duration of the working day. These and other default parameters and intermediate calculations needed to obtain the output data are described in Table 3. It was first assumed that, after collecting all the waste from the curb-side waste containers, if neither the volume, mass, nor time limits have been reached, then the truck will travel to the unloading site, unload its content there, and then go back to the parking area. If, however, during the collection route the truck reaches its maximum capacity either by weight or volume, then it will also go to unload its content, and then the algorithm in the model evaluates whether there is still enough time (the third limiting factor) to go back and continue the collection. If yes, the same truck is then assumed to return to the collection area and continue collecting—this iterative process is allowed to occur up to 3 times.
If adopting the same basic model as for a conventional truck, the utilization ratio may be calculated as:
U r = W T / ( N × P l )
where WT is the total waste mass collected per year and N is the number of trips per year.
A variable utilization ratio of the collection truck could instead be calculated as described in Equation (13):
U r = ( W T N ( P l W b o x ) × ( D 1 + D 4 + ( N 1 ) D 3 ) D T × r 1 ) + ( W T N ( P l W b o x ) × N D 3 D T × r 2 ) + ( W T N ( P l W b o x ) × D 2 D T × r 3 )
where DT is the distance of one complete trip (km); N is the number of trips (-); r1 is the effective load while the truck travels empty (-); r2 is the effective load while the truck travels full (-); and r3 is the effective load while the truck is collecting waste (-).
Taking into account the values for the effective load of the truck in each individual leg of the route (r1 = 0, r2 = 1 and r3 = 0.5), Equation (13) may be simplified as described in Equation (14).
U r = ( W T N ( P l W b o x ) ) × ( N D 3 D T + D 2 2 D T )
However, based on the experimental fuel consumption values obtained for a number of collection routes in the north of Spain (Galicia), it was found that in virtually all cases, the resulting βj factor for a truck of 20–26 t of maximum authorized weight and 17.3 of payload capacity (in relation to the corresponding collection truck) was invariably around 2. It was therefore decided to refrain from implementing this additional level of complexity in the model, and instead settle for using the simpler Equation (12) for the calculation of Ur, and then applying a fixed parameter βj = 2 throughout.
The additional fuel consumption to lift the containers and compress the waste (Add_diesel) was modeled assuming that the truck uses the same amount of fuel per hour as when traveling on urban roads, since it was impossible to obtain the additional fuel consumption due to these operations from experimental sources:
A d d _ d i e s e l   =   C   × *   T c o m p   ×   F c o m p
where C is the number of containers (or collection stops) (-); Tcomp is the average time spent in emptying one container and compacting the waste contained therein (or the correspondent amount spent at a collection stop) (h), which depends on the type of container used; and Fcomp is the diesel consumption factor while the truck is lifting containers and compacting waste (kg(diesel)/h), which was set by adopting the average fuel consumption of conventional trucks when traveling on urban roads at a speed used of 27 km/h.
Finally, the total fuel consumption of a waste collection vehicle (DieselTCT) (kg(diesel)) results from Equation (16):
D i e s e l T C T = ( j = 1 2 β j × D i e s e l c f ) × W T × D T + A d d _ d i e s e l
where WT is the total amount of waste collected (kg) and DT refers to one complete trip of the waste collection truck (km).
In the same way, the formulae to calculate the emissions of substances associated to diesel consumption were corrected using adapted βj factors and additional emission amounts.

4. Results

This section is divided into three main parts. Firstly, the performance of the existing methods (ORWARE, MSW-DST, and Ecoinvent) in predicting the performance of the collection trucks in terms of fuel (diesel) consumption in comparison to the experimental data from the known collection routes in Portugal (see Table 4) is presented. Secondly, the performance of the FENIX model in comparison to the aforementioned methods as well as experimental data are shown. Finally, the FENIX model’s ability to accurately estimate the environmental performance of the collection phase when selected changes are made to the operational parameters is discussed.

4.1. Comparison of Experimental Data to Results of Existing Models

Average experimental data from the 14 curb-side collection routes in Portugal are presented in Table 3. The experimental data on total fuel consumption were then compared with the results obtained by multiplying the default consumption rates assumed by ORWARE, MSW-DST, and Ecoinvent by the experimental data gathered in terms of total amount of waste (t), transport and effective collection distances (km), number of containers (-) and idling time while stopped to lift up the containers (h). Results of this comparison are shown in Figure 3. Vertical axes are expressed in a base-2 logarithmic scale.
An analysis of the results reveals that, overall, none of the total fuel consumption figures produced by these models match the experimental data. Only in those cases in which the characteristics of the experimental routes happened to coincide somehow with those of the calibration routes on which the average fuel consumption rates used in the models are based, were the results any better. In other cases, for instance for light packaging waste, the model estimates were found to be low by a factor of 4, when using Ecoinvent and ORWARE. In general, it was confirmed that if the objective of an LCA is to predict the potential impacts of a specific waste collection option, or to compare and choose among different alternatives, the use of models based on fixed ‘average’ fuel consumption factors may lead to rather inaccurate results.

4.2. Comparison of FENIX Model Results to Those Produced by Previous Models and to Experimental Data

The results produced by the FENIX model were also checked against the experimental data from the 14 curb-side collection routes in Portugal, for which all required input data included in Table 4 were gathered. The results of this comparison are shown in Table 5. This revealed that, on average, the FENIX model produces much more balanced and accurate results than all other models, and for all waste routes. This is quantitatively proven by the sum of the squared deviations of the results of each individual model vs. the experimental data.

4.3. Sensitivity to Model Parameters

The main reason for developing the FENIX model was the identified need for a model which would be able to predict changes in the environmental performance of the waste collecting phase before changes in operational parameters are applied in real life, in order to help decision makers to make environmentally and economically sound choices.
Table 6 presents some illustrative examples in which the potential effects of the variation of some of these operational parameters are assessed. Specifically, the following aspects were analyzed: the total number of containers (scenarios 1–2), the collection frequency (3–4), the length of the working day (5–6), and, finally, the collection in more rural areas (7–8). The latter was parameterized by increasing the distances between the parking area and the collection area, between the collection area and the unloading point, and from the unloading point back to the parking area, as well as increasing the distance between the individual collection sites within the collection area (a distance along which no effective waste collection is carried out).
As it can be seen, by reducing the number of containers in scenario 1 from 449 to 269 (the latter being the minimum number of containers calculated by the model as necessary for this particular route), or by increasing the number of containers by 10% (scenario 2), the performance of the collection phase (L/t was respectively improved by ~25% or worsened by ~17%. Increasing the collection frequency by 25% (scenario 3), or doubling it (scenario 4), produced a worsening in the performance by ~41% and ~120%, respectively. Changes in the duration of the working day (the new limiting factor included in this model) also had a large effect on the results. Reducing the available time by 2 h (scenario 5) or by one half (scenario 6) led to a worsening in the performance by ~32% and ~46%, respectively. Finally, collecting the same amount of waste with the same operational parameters but in more rural areas, exemplified by doubling the distances in the collection route and also considering 25 (scenario 7) or 50 (scenario 8) additional km traveled to reach the collection site, produced a worsening of the performance by ~68% and ~87% respectively.

5. Discussion

When performing LCAs of waste management systems, the environmental benefits of recycling must often be balanced against the additional environmental impacts arising from increased transportation [74]. As has been demonstrated by experimental results, using fixed consumption factors may lead to some serious shortcomings in calculating the environmental impact of the collection phase, especially when the characteristics of the real collection routes do not coincide with those that were used to derive the default consumption factors. In particular, the effects of changes in operational parameters of the waste collection route on the fuel consumption rates have been discussed in the previous section and shown in Table 6. However, the effect of time (in terms of the overall duration of the waste collection trip) merits special attention and additional discussion.
In the guidelines for conducing LCA of waste management systems developed in the last decades [65,75], time is not given any consideration, and only the overall volume and weight of the waste are mentioned as limiting factors to be considered for the calculation of the environmental impacts of the collection and transport of waste. In addition, other studies evaluating the significance of the collection and transport phases in LCAs of integrated waste management systems indicate that ”time is not relevant for assessing the environmental loads of waste collection“ [57,76]. However, this assertion appears to be questionable based on the results illustrated in Table 6, where changes in the duration of the waste collection journey were found to have an important effect on the results. In fact, once the maximum allotted time for the collection of waste is reached, it no longer matters whether there is any capacity available left in the truck, since the truck will still return to the parking area and another truck will resume the collection on the following day from where it was interrupted. In so doing, the total cumulative distance traveled to collect the same overall amount of waste will increase, thereby negatively affecting the average collection performance in terms of L(diesel)/t(waste collected). The time factor may not have a significant influence in urban areas, but it does have a larger influence in more rural areas, where long distances are driven so waste collection is less efficient to begin with.
This is particularly relevant for countries like Spain and Portugal, where the performance of the waste collection phase is often far from optimal. In these countries a large percentage of municipalities under the obligation of implementing source-separated collection systems have less than 5000 inhabitants. Moreover, collection frequencies are much higher than in other countries. Whereas in Denmark, for instance, collection for paper and glass waste is carried out once or twice per month [76], in Spain the collection frequency is typically once per week and in Portugal twice per month. In the case of MSW, the situation is even more extreme. In Denmark, MSW is collected from 2 to 4 times per month, whereas in Spain and Portugal, MSW is typically collected every 1 to 3 days. This situation leads to higher fuel consumption rates, in terms of liters of diesel per ton of collected waste, than in other countries. The higher intensity in collection frequency may be due to specific climate conditions with result in a more rapid decomposition of organic waste (especially in the summer), which causes undesirable odors and inconvenience to citizens, but may also be partly due to perceived citizen demand.

6. Conclusions

As discussed in the previous sections, it is safe to conclude that the fixed consumption rates included in some LCA tools or databases for waste management to calculate the environmental performance of the waste collection phase are to be used warily. If the aim of the study at hand is to evaluate the environmental performance of the currently implemented waste collection system, real fuel consumption data should be used instead, while adjusting the characteristics of the route on which the average parameters are based to match the characteristics of the real-world system under analysis. Conversely, for some applications, especially if the focus of the study is the optimization of the collection phase itself, and where predictive results are needed before implementing changes in the system, it is arguably necessary to use a more complex model (such as the FENIX model presented here), duly taking into account many more characteristics of the collection scheme and the associated operational parameters in the model itself, in which consumption and emission factors depend on the characteristics of the route and are not fixed. Specifically, one parameter which has been identified as particularly relevant in the development of the FENIX model, but which had hitherto been neglected in most previously available models, is the duration of the working day. The recommendation is thus made to pay special attention to this parameter in all future LCA modeling of waste collection.

Author Contributions

Conceptualization, A.B. and M.R.; methodology, A.B. and M.R.; data collection: C.A.T.; new model development, A.B., M.R., P.F.-i.-P. and A.F.; validation: F.P.-M.; formal analysis, A.B.; writing—original draft preparation, A.B. and M.R.; writing—review and editing, A.B.; supervision, P.F.-i.-P. All authors have read and agreed to the published version of the manuscript.

Funding

This research was funded by the FENIX Project, LIFE08/ENV/E/000135.

Institutional Review Board Statement

Not applicable.

Informed Consent Statement

Not applicable.

Data Availability Statement

Not applicable.

Acknowledgments

The authors of this paper want to extend their acknowledgements to the FENIX Project (LIFE08/ENV/E/000135), and especially to the Green Dot Holders of Spain and Portugal, Ecoembalajes España and Sociedade Ponto Verde, for their continuous help throughout the project and the critical review of the model, using their broad and practical experience. This work is supported as well by National Funds by FCT—Portuguese Foundation for Science and Technology, under the project UIDB/04033/2020.

Conflicts of Interest

The authors declare no conflict of interest. The funders had no role in the design of the study; in the collection, analyses, or interpretation of data; in the writing of the manuscript, or in the decision to publish the results.

References

  1. Hauschild, M.; Barlaz, M.A. LCA in Waste Management: Introduction to Principle and Method. In Solid Waste Technology & Management; Christensen, T.H., Ed.; John Wiley & Sons, Ltd.: Chichester, UK, 2010; Volume 1, pp. 111–136. [Google Scholar]
  2. Laurent, A.; Bakas, I.; Clavreul, J.; Bernstad, A.; Niero, M.; Gentil, E.; Hauschild, M.Z.; Christensen, T.H. Review of LCA studies of solid waste management systems–Part I: Lessons learned and perspectives. Waste Manag. 2014, 34, 573–588. [Google Scholar] [CrossRef] [PubMed]
  3. Khandelwal, H.; Dhar, H.; Thalla, A.K.; Kumar, S. Application of life cycle assessment in municipal solid waste management: A worldwide critical review. J. Clean. Prod. 2019, 209, 630–654. [Google Scholar] [CrossRef]
  4. Iqbal, A.; Liu, X.; Chen, G.-H. Municipal solid waste: Review of best practices in application of life cycle assessment and sustainable management techniques. Sci. Total Environ. 2020, 729, 138622. [Google Scholar] [CrossRef] [PubMed]
  5. Zhang, J.; Qin, Q.; Li, G.; Tseng, C.-H. Sustainable municipal waste management strategies through life cycle assessment method: A review. J. Environ. Manag. 2021, 287, 112238. [Google Scholar] [CrossRef] [PubMed]
  6. Finnveden, G.; Ekvall, T. Life-cycle assessment as a decision-support tool—the case of recycling versus incineration of paper. Resour. Conserv. Recycl. 1998, 24, 235–256. [Google Scholar] [CrossRef]
  7. Güereca, L.P.; Gassó, S.; Baldasano, J.M.; Jiménez-Guerrero, P. Life cycle assessment of two biowaste management systems for Barcelona, Spain. Resour. Conserv. Recycl. 2006, 49, 32–48. [Google Scholar] [CrossRef]
  8. Merrild, H.; Damgaard, A.; Christensen, T.H. Life cycle assessment of waste paper management: The importance of technology data and system boundaries in assessing recycling and incineration. Resour. Conserv. Recycl. 2008, 52, 1391–1398. [Google Scholar] [CrossRef]
  9. Villanueva, A.; Wenzel, H. Paper waste–Recycling, incineration or landfilling? A review of existing life cycle assessments. Waste Manag. 2007, 27, S29–S46. [Google Scholar] [CrossRef] [PubMed]
  10. Wollny, V.; Dehoust, G.; Fritsche, U.R.; Weinem, P. Comparison of Plastic Packaging Waste Management Options: Feedstock Recycling versus Energy Recovery in Germany. J. Ind. Ecol. 2001, 5, 49–63. [Google Scholar] [CrossRef]
  11. Lazarevic, D.; Aoustin, E.; Buclet, N.; Brandt, N. Plastic waste management in the context of a European recycling society: Comparing results and uncertainties in a life cycle perspective. Resour. Conserv. Recycl. 2010, 55, 246–259. [Google Scholar] [CrossRef]
  12. Rigamonti, L.; Grosso, M.; Møller, J.; Sanchez, V.M.; Magnani, S.; Christensen, T. Environmental evaluation of plastic waste management scenarios. Resour. Conserv. Recycl. 2014, 85, 42–53. [Google Scholar] [CrossRef]
  13. Kim, M.H.; Song, H.B.; Song, Y.; Jeong, I.T.; Kim, J.W. Evaluation of food waste disposal options in terms of global warming and energy recovery: Korea. Int. J. Energy Environ. Eng. 2013, 4, 1. [Google Scholar] [CrossRef][Green Version]
  14. Ahamed, A.; Yin, K.; Ng, B.; Ren, F.; Chang, V.-C.; Wang, J.-Y. Life cycle assessment of the present and proposed food waste management technologies from environmental and economic impact perspectives. J. Clean. Prod. 2016, 131, 607–614. [Google Scholar] [CrossRef]
  15. Edwards, J.; Othman, M.; Crossin, E.; Burn, S. Life cycle assessment to compare the environmental impact of seven contemporary food waste management systems. Bioresour. Technol. 2018, 248, 156–173. [Google Scholar] [CrossRef] [PubMed]
  16. Margallo, M.; Aldaco, R.; Irabien, A.; Carrillo, V.; Fischer, M.; Bala, A.; Fullana, P. Life cycle assessment modelling of waste-to-energy incineration in Spain and Portugal. Waste Manag. Res. 2014, 32, 492–499. [Google Scholar] [CrossRef] [PubMed]
  17. Arena, U.; Ardolino, F.; Di Gregorio, F. A life cycle assessment of environmental performances of two combustion- and gasification-based waste-to-energy technologies. Waste Manag. 2015, 41, 60–74. [Google Scholar] [CrossRef] [PubMed]
  18. Di Maria, F.; Micale, C. Life cycle analysis of incineration compared to anaerobic digestion followed by composting for managing organic waste: The influence of system components for an Italian district. Int. J. Life Cycle Assess. 2015, 20, 377–388. [Google Scholar] [CrossRef]
  19. Lombardi, L.; Carnevale, E.A. Evaluation of the environmental sustainability of different waste-to-energy plant configurations. Waste Manag. 2018, 73, 232–246. [Google Scholar] [CrossRef] [PubMed]
  20. Dong, J.; Tang, Y.; Nzihou, A.; Chi, Y.; Weiss-Hortala, E.; Ni, M. Life cycle assessment of pyrolysis, gasification and incineration waste-to-energy technologies: Theoretical analysis and case study of commercial plants. Sci. Total Environ. 2018, 626, 744–753. [Google Scholar] [CrossRef]
  21. Denison, R.A. Environmental Life-Cycle Comparisons of Recycling, Landfilling, and Incineration: A Review of Recent Studies. Annu. Rev. Energy Environ. 1996, 21, 191–237. [Google Scholar] [CrossRef][Green Version]
  22. Muñoz, I.; Rieradevall, J.; Domènech, X.; Milà, L. LCA application to integrated waste management planning in Gipuzkoa (Spain). Int. J. Life Cycle Assess. 2004, 9, 272–280. [Google Scholar] [CrossRef]
  23. Liikanen, M.; Havukainen, J.; Hupponen, M.; Horttanainen, M. Influence of different factors in the life cycle assessment of mixed municipal solid waste management systems–A comparison of case studies in Finland and China. J. Clean. Prod. 2017, 154, 389–400. [Google Scholar] [CrossRef]
  24. Saraiva, A.B.; Souza, R.; Valle, R. Comparative lifecycle assessment of alternatives for waste management in Rio de Janeiro–Investigating the influence of an attributional or consequential approach. Waste Manag. 2017, 68, 701–710. [Google Scholar] [CrossRef] [PubMed][Green Version]
  25. Chen, G.; Wang, X.; Li, J.; Yan, B.; Wang, Y.; Wu, X.; Velichkova, R.; Cheng, Z.; Ma, W. Environmental, energy, and economic analysis of integrated treatment of municipal solid waste and sewage sludge: A case study in China. Sci. Total Environ. 2019, 647, 1433–1443. [Google Scholar] [CrossRef] [PubMed]
  26. Iqbal, A.; Zan, F.; Liu, X.; Chen, G.-H. Integrated municipal solid waste management scheme of Hong Kong: A comprehensive analysis in terms of global warming potential and energy use. J. Clean. Prod. 2019, 225, 1079–1088. [Google Scholar] [CrossRef]
  27. Paes, M.X.; de Medeiros, G.A.; Mancini, S.D.; Bortoleto, A.P.; de Oliveira, J.A.P.; Kulay, L.A. Municipal solid waste management: Integrated analysis of environmental and economic indicators based on life cycle assessment. J. Clean. Prod. 2020, 254, 119848. [Google Scholar] [CrossRef]
  28. Fernández-Nava, Y.; del Río, J.; Rodríguez-Iglesias, J.; Castrillón, L.; Marañón, E. Life cycle assessment of different municipal solid waste management options: A case study of Asturias (Spain). J. Clean. Prod. 2014, 81, 178–189. [Google Scholar] [CrossRef][Green Version]
  29. Beigl, P.; Salhofer, S. Comparison of ecological effects and costs of communal waste management systems. Resour. Conserv. Recycl. 2004, 41, 83–102. [Google Scholar] [CrossRef][Green Version]
  30. Banar, M.; Cokaygil, Z.; Ozkan, A. Life cycle assessment of solid waste management options for Eskisehir, Turkey. Waste Manag. 2009, 29, 54–62. [Google Scholar] [CrossRef]
  31. Iriarte, A.; Gabarrell, X.; Rieradevall, J. LCA of selective waste collection systems in dense urban areas. Waste Manag. 2009, 29, 903–914. [Google Scholar] [CrossRef] [PubMed]
  32. Tulokhonova, A.; Ulanova, O. Assessment of municipal solid waste management scenarios in Irkutsk (Russia) using a life cycle assessment-integrated waste management model. Waste Manag. Res. 2013, 31, 475–484. [Google Scholar] [CrossRef] [PubMed]
  33. Kulczycka, J.; Lelek, Ł.; Lewandowska, A.; Zarebska, J. Life cycle assessment of municipal solid waste management–comparison of results using different LCA models. Polish J. Environ. Stud. 2015, 24, 125–140. [Google Scholar] [CrossRef]
  34. Rigamonti, L.; Grosso, M.; Sunseri, M.C. Influence of assumptions about selection and recycling efficiencies on the LCA of integrated waste management systems. Int. J. Life Cycle Assess. 2009, 14, 411–419. [Google Scholar] [CrossRef]
  35. Dri, M.; Canfora, P.; Antonopoulos, I.; Gaudillat, P. Best Environmental Management Practice for the Waste Management Sector; EUR 29136 EN; Publications Office of the European Union: Luxembourg, 2018; ISBN 978-92-79-80361-1. JRC111059. [Google Scholar] [CrossRef]
  36. Dalemo, M.; Sonesson, U.; Björklund, A.; Mingarini, K.; Frostell, B.; Jönsson, H.; Nybrant, T.; Sundqvist, J.-O.; Thyselius, L. ORWARE–A simulation model for organic waste handling systems. Part 1: Model description. Resour. Conserv. Recycl. 1997, 21, 17–37. [Google Scholar] [CrossRef]
  37. Eriksson, O.; Frostell, B.; Björklund, A.; Assefa, G.; Sundqvist, J.-O.; Granath, J.; Carlsson, M.; Baky, A.; Thyselius, L. ORWARE—a simulation tool for waste management. Resour. Conserv. Recycl. 2002, 36, 287–307. [Google Scholar] [CrossRef]
  38. Haight, M. EPIC/CSR Integrated Solid Waste Management Model Final Report; Technical Report. Waterloo, ON, Canada, 1999; p. 23. Available online: https://uwaterloo.ca/integrated-waste-management-model-for-municipalities/sites/ca.integrated-waste-management-model-for-municipalities/files/uploads/files/tech_report_mar9_2004.pdf (accessed on 20 March 2021).
  39. Haight, M. Integrated Solid Waste Management Model Technical Report; University of Waterloo, School of Planning: Waterloo, ON, Canada, 2004; p. 101. [Google Scholar]
  40. EPIC & CSR Integrated Solid Waste Management’s Tool: Measuring the Environmental Performance of Waste Management Systems; Mississauda, ON, Canada, 2000.
  41. Weitz, K.; Barlaz, M.; Ranjithan, R.; Brill, D.; Thorneloe, S.; Ham, R. Life Cycle Management of Municipal Solid Waste. Int. J. Life Cycle Assess. 1999, 4, 195–201. [Google Scholar] [CrossRef]
  42. Thorneloe, S.A.; Weitz, K.; Jambeck, J. Application of the US decision support tool for materials and waste management. Waste Manag. 2007, 27, 1006–1020. [Google Scholar] [CrossRef][Green Version]
  43. Ecobilan Life Cycle Research Programme for Waste Management: Inventory Development for Waste Management Operations: Landfill Final Report; Environment Agency: Bristol, UK, 1997.
  44. McDougall, F.R.; White, P.R.; Franke, M.; Hindle, P. Integrated solid waste management: A Life Cycle Inventory. Int. J. Life Cycle Assess. 2001, 6, 320. [Google Scholar] [CrossRef]
  45. Tanaka, M.; Matsui, Y.; Nishimura, A. WLCA (Waste LCA) for Strategic Solid Waste Management. In Proceedings of the Proceedings of The Sixth International Conference on EcoBalance: Developing and systematizing of EcoBalance Tools based on Life-Cycle-Thinking, Tsukuba, Japan, 25–27 October 2004. [Google Scholar]
  46. Tanaka, M. Strategic Solid Waste Management: Challenges for Sustainable Society; Okayama University Press: Tokyo, Japan, 2008; p. 356. (In Japanese) [Google Scholar]
  47. Den Boer, E.; Den Boer, J.; Jager, J.; Rodrigo, J.; Meneses, M.; Castells, F.; Schanne, L. Deliverable Report on D3.1 and D3.2: Environmental Sustainability Criteria and Indicators for Waste Management (Work Package 3) The Use of Life Cycle Assessment Tool for the Development of Integrated Waste Management Strategies for Cities and Regions with Rapid Growing Economies; Technische Universitaet Darmstadt: Darmstadt, Germany, 2005. [Google Scholar]
  48. Den Boer, E.; Den Boer, J.; Jager, J. Waste Management Planning and optimisation. In Handbook for Municipal Waste Prognosis and Sustainability Assessment of Waste Management Systems; LCA-IWM: Darmstadt, Germany, 2005. [Google Scholar]
  49. Boer, J.D.; Jager, J. LCA-IWM: A decision support tool for sustainability assessment of waste management systems. Waste Manag. 2007, 27, 1032–1045. [Google Scholar] [CrossRef] [PubMed]
  50. Gentil, E.; Hall, D.; Thomas, B.; Shiels, S.; Collins, M. LCA Tool in Waste Management: New Features and Functionalities. In Proceedings of the Tenth International Waste Management and Landfill Symposium, Sardinia, Italy, 3–7 October 2005. [Google Scholar]
  51. Coleman, T. Life Cycle Assessment for Municipal Waste: Supporting Decisions. Resources Recovery Forum. Annual General Meeting. 19 July 2006. Available online: https://www.tdx.cat/bitstream/handle/10803/289634/abg1de1.pdf?sequence=1 (accessed on 20 March 2021).
  52. Kirkeby, J.T.; Birgisdottir, H.; Hansen, T.L.; Christensen, T.H.; Bhander, G.S.; Hauschild, M. Environmental assessment of solid waste systems and technologies: EASEWASTE. Waste Manag. Res. 2006, 24, 3–15. [Google Scholar] [CrossRef]
  53. Clavreul, J.; Baumeister, H.; Christensen, T.H.; Damgaard, A. An environmental assessment system for environmental technologies. Environ. Model. Softw. 2014, 60, 18–30. [Google Scholar] [CrossRef][Green Version]
  54. Levis, J.W.; Barlaz, M.A.; DeCarolis, J.F.; Ranjithan, S.R. A generalized multistage optimization modeling framework for life cycle assessment-based integrated solid waste management. Environ. Model. Softw. 2013, 50, 51–65. [Google Scholar] [CrossRef]
  55. White, P.R.; Franke, M.; Hindle, P. Integrated Solid Waste Management: A Lifecycle Inventory; Blackie Academic and Professional: London, UK, 1995. [Google Scholar]
  56. Gentil, E.C.; Damgaard, A.; Hauschild, M.; Finnveden, G.; Eriksson, O.; Thorneloe, S.; Kaplan, P.O.; Barlaz, M.; Muller, O.; Matsui, Y.; et al. Models for waste life cycle assessment: Review of technical assumptions. Waste Manag. 2010, 30, 2636–2648. [Google Scholar] [CrossRef] [PubMed]
  57. Björklund, A.; Finnveden, G.; Roth, L. Application of LCA in Waste Management. In Solid Waste Technology & Management; Wiley: Hoboken, NJ, USA, 2010; Volume 1&2, pp. 137–160. [Google Scholar]
  58. Hansen, T.L.; Christensen, T.H.; Schmidt, S. Environmental modelling of use of treated organic waste on agricultural land: A comparison of existing models for life cycle assessment of waste systems. Waste Manag. Res. 2006, 24, 141–152. [Google Scholar] [CrossRef] [PubMed]
  59. Winkler, J.; Bilitewski, B. Comparative evaluation of life cycle assessment models for solid waste management. Waste Manag. 2007, 27, 1021–1031. [Google Scholar] [CrossRef]
  60. Rimaityte, I.; Denafas, G.; Jager, J. Report: Environmental assessment of Darmstadt (Germany) municipal waste incineration plant. Waste Manag. Res. 2007, 25, 177–182. [Google Scholar] [CrossRef] [PubMed]
  61. Sonesson, U. Modelling of waste collection–a general approach to calculate fuel consumption and time. Waste Manag. Res. J. Sustain. Circ. Econ. 2000, 18, 115–123. [Google Scholar]
  62. Ekvall, T.; Finnveden, G. The Application of Life Cycle Assessment to Integrated Solid Waste Management. Process. Saf. Environ. Prot. 2000, 78, 288–294. [Google Scholar] [CrossRef]
  63. Eriksson, O.; Reich, M.C.; Frostell, B.; Björklund, A.; Assefa, G.; Sundqvist, 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][Green Version]
  64. Larsen, A.W. Environmental Assessment of Waste Collection Seen in a System Perspective; Technical University of Denmark: Lyngby, Denmark, 2009. [Google Scholar]
  65. European Union. Supporting Environmentally Sound Decisions for Waste Management–A Technical Guide to Life Cycle Thinking (LCT) and Life Cycle Assessment (LCA) for Waste Experts and LCA Practitioners; Publications Office of the European Union: Luxembourg, 2011; ISSN 1831-9424. (online). [Google Scholar]
  66. Directive 2008/98/EC of the European Parliament and of the Council of 19 November 2008 on waste and repealing certain Directives. Official Journal of the European Union L312, 22 of November 2008. pp. 3–30. Available online: https://eur-lex.europa.eu/LexUriServ/LexUriServ.do?uri=OJ:L:2008:312:0003:0030:en:PDF (accessed on 20 March 2021).
  67. Klang, A.G. Sustainable Waste Management. Methods and Framework for Analysis. Ph.D. Thesis, Norwegian University of Science and Technology, Trondheim, Norway, 2005. [Google Scholar]
  68. Tanskanen, J.-H.; Kaila, J. Comparison of methods used in the collection of source-separated household waste. Waste Manag. Res. 2001, 19, 486–497. [Google Scholar] [CrossRef] [PubMed]
  69. Salhofer, S.; Schneider, F.; Obersteiner, G. The ecological relevance of transport in waste disposal systems in Western Europe. Waste Manag. 2007, 27, S47–S57. [Google Scholar] [CrossRef] [PubMed]
  70. Aryan, Y.; Yadav, P.; Samadder, S.R. Life Cycle Assessment of the existing and proposed plastic waste management options in India: A case study. J. Clean. Prod. 2019, 211, 1268–1283. [Google Scholar] [CrossRef]
  71. Sonesson, U. Modelling of the Compost and Transport Process in the ORWARE Simulation Model; Department of Agricultural Engineering, Swedish University of Agricultural Sciences: Uppsala, Sweden, 1996; p. 35. [Google Scholar]
  72. Curtis, E.M.; Dumas, R.D. A Spreadsheet Process Model for Analysis of Costs and Life-Cycle Inventory Parameters Associated With Collection of Municipal Solid Waste; North Carolina State University: Raleigh, NC, USA, 2000; p. 272. [Google Scholar]
  73. Doka, G. Life Cycle Inventories of Waste Treatment Services. Ecoinvent Report no 13; Swiss Centre for Life Cycle Inventories: Dübendorf, Switzerland, 2009. [Google Scholar]
  74. Baumann, H.; Tillman, A.-M. The Hitch Hiker’s Guide to LCA: An Orientation in Life Cycle Assessment Methodology and Applications; Studentlitteratur: Lund, Sweden, 2004. [Google Scholar]
  75. Bjarnadóttir, H.J.; Friðriksson, G.B.; Johnsen, T.; Sletsen, H. Guidelines for the Use of LCA in the Waste Management Sector; Nordtest Report TR 517; Nordtest: Espoo, Finland, 2002. [Google Scholar]
  76. Larsen, A.W.; Vrgoc, M.; Christensen, T.H.; Lieberknecht, P. Diesel consumption in waste collection and transport and its environmental significance. Waste Manag. Res. 2009, 27, 652–659. [Google Scholar] [CrossRef] [PubMed]
Figure 1. Research steps.
Figure 1. Research steps.
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Figure 2. Simplified diagram of the collection model to calculate distances, share of km in each type of service, and utilization ratio.
Figure 2. Simplified diagram of the collection model to calculate distances, share of km in each type of service, and utilization ratio.
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Figure 3. Comparison of the results of experimental data with the results using Ecoinvent, ORWARE, and MSW-DST model for (a) glass; (b) mixed waste; (c) light packaging waste; and (d) paper and cardboard.
Figure 3. Comparison of the results of experimental data with the results using Ecoinvent, ORWARE, and MSW-DST model for (a) glass; (b) mixed waste; (c) light packaging waste; and (d) paper and cardboard.
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Table 1. The most widely known, used, and complete waste LCA models.
Table 1. The most widely known, used, and complete waste LCA models.
SoftwareCountryLaunch TimeReference
ORWARE (a)Sweden1997[36,37]
EPIC/CSR (b)CA1999[38,39,40]
MSW-DTS (c)USA1999[41,42]
WIZARD (d)UK, FR, NZ1999[43]
IWM-2 (e)United Kingdom2001[44]
SSWMSS (f)Japan2004[45,46]
LCA IWM (g)European Union2005[47,48,49]
WRATE (h)United Kingdom2007[50,51]
EASEWASTE (i)Denmark2008–2009[52]
EASETECH (j)Denmark2013[53]
SWOLF (k)USA2014[54]
Notes: (a) ORWARE (ORganic WAste REsearch) was initially focused on organic waste but extended afterwards to other waste fractions. (b) EPIC/CSR is an Integrated Waste Management model produced by the Environment and Plastics Industry Council (EPIC) and Corporations Supporting Recycling (CSR). (c) MSW-DST (Municipal Solid Waste Decision Support Tool). (d) WIZARD (Waste-Integrated Systems Assessment for Recovery and Disposal). (e) Integrated Waste Management (IWM), first version launched in 1995 [55]. (f) SSWMSS (Strategic Solid Waste Management Supporting Software). (g) LCA IWM (Life Cycle Assessment-Integrated Waste Management) software was developed under a research project financed by the European Commission between 2002 and 2005. It also includes a prognostic tool for estimating the future generation of waste in European Cities. (h) WRATE (Waste and Resources Assessment Tool for the Environment) software is an evolution of the older WIZARD. (i) EASEWASTE (Environmental Assessment of Solid Waste Systems and Technologies). (j) EASETECH (Environmental Assessment System for Environmental TECHnologies) is an evolution of the older EASEWASTE. (k) SWOLF (Solid Waste Optimization Life-Cycle Framework). Information extracted from Gentil et al., 2010 and updated [56].
Table 2. Default diesel consumption rates used in the analyzed models.
Table 2. Default diesel consumption rates used in the analyzed models.
Units of Energy ConsumptionWaste Truck, in Collecting RouteWaste Truck, from the Collection Area to the Unloading PointWaste Truck, Idling
ORWARE (a)L/(t.km)0.240.13
MSW-DST (a)L/km1.180.47
L/h 0.26
EcoinventL/(t.km)0.42
Notes: (a) original consumption rates were transformed to international system (SI) units.
Table 3. Main operational data included in the model to calculate model key parameters.
Table 3. Main operational data included in the model to calculate model key parameters.
Input DataDefault Parameters and Intermediate Calculations
WT: total amount of waste collected (kg)
dens: waste density (kg/m3)
Freq: collection frequency (year-1)
C: number of containers (-)
Vc: average volume per container (m3/C)
Vt: volume capacity of the truck (m3/truck)
D1: distance between the parking lot and the collection route (a) (km)
D3: distance from the collection area (a) to the unloading site (km)
Dc: distance in between individual containers (km/C)
D4: distance between the unloading site and the parking lot (km)
TT: duration of the working day (h)
βj: consumption truck correction factor (-)
Pl: maximum payload capacity of the truck (kgload)
Aj: diesel consumption of the empty truck, depending on the type of road (kgdiesel/km)
Bj: diesel consumption of the full truck, depending on the type of road (kgdiesel/km)
Fcomp: diesel consumption factor while the truck is lifting containers and compacting waste (kgdiesel/h)
Wbox: weight of the box truck (kg)
Fillc: average container fill ratio (%)
crt: compaction ratio of the truck (-)
ef: collection efficiency in number of containers collected per hour (C/h)
Scol: average speed while collecting (km/h)
Stransp: average speed while transporting (km/h)
Tcomp: time spent loading and compacting waste (h)
Tunload: time spent unloading waste (h)
Tluch: time for lunch break (h)
Ttransp: total time spent while transporting (h)
Tcol: time spent collecting (h)
D2: total distance spent while collecting waste (effective collection distance) (km)
N: number of trips per truck (-)
Output Data
αj: share of km traveled in each type of road (-)
Ur: utilization (fill) ratio of the truck by mass (-)
DT: distance of one full trip of the waste collection truck (km)
(a) This distance is modeled as the weighted mean distance to the different collection points within the collection area.
Table 4. Average experimental data of different curb-side collection routes in Portugal.
Table 4. Average experimental data of different curb-side collection routes in Portugal.
Waste Fraction CollectedRoute CodeAmount Collected (t/year)Annual Distance (km/year)Annual Diesel Consumption (L/year)Performance Indicators
L/100 kmL/t
GlassG11895996171628.69.1
G2124263775528.66.1
MSWMSW1203922,91924,935108.812.2
MSW2301547,26530,21663.910.0
MSW3199035,07823,47566.911.8
Light Packaging WasteLP1763877195650.425.6
LP2 (a)1392990176559.112.7
LP31655347439082.126.6
LP49221472335108.825.3
Paper and CardboardP11442773160657.911.2
P2 (a)2482584152559.16.2
P32936747554082.118.9
P420126512884108.814.4
P53325788387366.911.7
(a) Correspond to the more commercial routes, which are more efficient in environmental performance (L/t).
Table 5. Comparison of FENIX results with experimental and existing models.
Table 5. Comparison of FENIX results with experimental and existing models.
Waste Fraction CollectedRoute CodeExperimental(L/t)Relative Deviation from Experimental Data
FENIXORWAREMSW-DSTEcoinvent
GlassG19.1−0.340.54−0.040.70
G26.10.200.920.851.25
MSWMSW112.20.44−0.19−0.69−0.26
MSW210.0−0.110.46−0.550.07
MSW311.80.630.06−0.62−0.34
Light Packaging WasteLP125.6−0.11−0.480.57−0.38
LP212.7−0.13−0.090.480.22
LP326.6−0.25−0.66−0.01−0.58
LP425.30.26−0.73−0.27−0.69
Paper and CardboardP111.2−0.01−0.170.20−0.19
P26.20.120.480.360.80
P318.9−0.11−0.38−0.02−0.26
P414.40.19−0.45−0.31−0.42
P511.70.65−0.27−0.48−0.41
Sum of the squared deviations 1.413.273.014.35
Table 6. Effects of selected operational parameters of the route on the waste collection performance.
Table 6. Effects of selected operational parameters of the route on the waste collection performance.
INPUT DATACALCULATED DATA
Waste (t)Working Day (h)Yearly Freq.N. ContContainer Volume (m3)Truck Volume (m3)Dist Parking-Fist ContDist End Coll-UnloadingDist Unloading Point -ParkingDist between Collection AreasPerformance (n.cont/h)(kg diesel/(t.km))Annual km Traveledkm/tripl/yearl/t
Baseline92.28554490.25221.710.210.7041.20.863462312928.4831.76
192.28552690.25221.710.210.7041.20.492184402171.1323.55
292.28554940.25221.710.210.7041.21.003462313419.5537.09
392.28704490.25221.710.210.7041.21.204406314123.5944.72
492.281104490.25221.710.210.7041.21.886923316435.0369.79
592.26554490.25221.710.210.7041.21.204739293853.3341.79
692.24554490.25221.710.210.7041.21.446016274280.6446.43
792.28554490.25223.420.421.42539.30.677257664915.8153.32
892.28554490.25223.420.421.45037.50.648602785469.5059.32
Note: Changes with respect to the baseline scenario are marked in bold.
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Bala, A.; Raugei, M.; Teixeira, C.A.; Fernández, A.; Pan-Montojo, F.; Fullana-i-Palmer, P. Assessing the Environmental Performance of Municipal Solid Waste Collection: A New Predictive LCA Model. Sustainability 2021, 13, 5810. https://doi.org/10.3390/su13115810

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Bala A, Raugei M, Teixeira CA, Fernández A, Pan-Montojo F, Fullana-i-Palmer P. Assessing the Environmental Performance of Municipal Solid Waste Collection: A New Predictive LCA Model. Sustainability. 2021; 13(11):5810. https://doi.org/10.3390/su13115810

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Bala, Alba, Marco Raugei, Carlos Afonso Teixeira, Alberto Fernández, Francisco Pan-Montojo, and Pere Fullana-i-Palmer. 2021. "Assessing the Environmental Performance of Municipal Solid Waste Collection: A New Predictive LCA Model" Sustainability 13, no. 11: 5810. https://doi.org/10.3390/su13115810

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