Environmental Impacts of Charging Concepts for Battery Electric Vehicles: A Comparison of On-Board and Off-Board Charging Systems Based on a Life Cycle Assessment

<jats:p>We investigate the environmental impacts of on-board (based on alternating current, AC) and off-board (based on direct current, DC) charging concepts for electric vehicles using Life Cycle Assessment and considering a maximum charging power of 22 kW (AC) and 50 kW (DC). Our results show that the manufacturing of chargers provokes the highest contribution to environmental impacts of the production phase. Within the chargers, the filters could be identified as main polluters for all power levels. When comparing the results on a system level, the DC system causes less environmental impact than the AC system in all impact categories. In our diffusion scenarios for electric vehicles, annual emission reductions of up to 35 million kg CO2-eq. could be achieved when the DC system is used instead of the AC system. In addition to the environmental assessment, we examine economic effects. Here, we find annual savings of up to 8.5 million euros, when the DC system is used instead of the AC system.</jats:p>

section_content: As the average temperature on earth is increasing [1] [2] [3], both environmental and economic consequences are to be expected [4, 5]. Hence, there are international efforts to reduce this rise to below 2 • C in the long-term and binding targets have been agreed in the Kyoto Protocol and the Paris Agreement, among others [5, 6]. 

Being one of the largest global economies, Germany emitted ≈858 mn. tons of CO 2 -equivalent (CO 2 -eq. ) in 2018, 19% of which originated in the transport sector [7]. Within the transport sector, passenger cars are a major source of emissions [8]. Modern, non-fossil fuel-based propulsion systems offer opportunities to reduce the emissions and thereby help to mitigate climate change and to reduce Energies 2020, 13, 6508 3 of 31 at home, a 3. 7 kW charging point (AC) is available. Charging with 3. 7 kW requires no additional power electronics. 2. 

In our DC system, each electric vehicle is equipped with an OBC with 3. 7 kW charging power that allows for charging at home (AC). Additionally, all electric vehicles can be charged with an OfBC with 50 kW charging power at publicly accessible charging points (DC). 

Please note that the introduced names of our systems are determined by the publicly accessible charging infrastructure. In the AC system, charging at public charging infrastructure is only possible with AC; in the DC system, charging at public charging infrastructure is only possible with DC. The AC OBC with 3. 7 kW in the DC system is used for a more realistic representation of the systems, but it does not constitute the name of the system. 

Furthermore, we differentiate between chargers and charging infrastructure (CIS). When talking about CIS, we consider the connection with the grid, the charging cable, and the housing of the charging station. The chargers in our study consist of the necessary power electronics and a housing for the power electronics. The power electronics essentially include the required converters, a filter, and additional electronic components such as printed circuit boards (PCBs) and busbars. The converters itself are composed of different electronic components such as diodes, MOSFETs, coils, capacitors, and transformers. 

As indicated in Table 1, the number of components either scale with the number of charging points, the number of charging stations (which can consist of more than one charging point), or the number of BEVs. 1 charging infrastructure can rather be a charging station or a charging point.
section_name: Introduction

section_content: To assess potential reductions of the environmental impact of charging infrastructure on a large scale, we introduce three scenarios regarding the diffusion of BEVs in Germany. Using the Bass diffusion model [23], we differentiate the following potential diffusion curves:
section_name: Scenarios

section_content: In the first scenario (S), the innovation and imitation coefficients of the Bass model are adopted from [24]. Although [24] data are based on data of global sales of hybrid Toyota vehicles, they are considered to be sufficiently good estimates. The values for the vehicle stock, the number of new registrations, and the number of retired passenger cars are taken from [25]. For a near future distribution, a vehicle stock of 170,000 vehicles is estimated, which seems to be reasonable (136,617 electric vehicles on 1 January 2020 in Germany [26] ).
section_name: •

section_content: The second scenario (M) is based on data by [27, 28], who state the objective that road traffic in Germany should be climate-neutral by 2050. One possibility of how this aim might be reached is to regulate the registration of new cars so that solely BEVs can be registered. For our estimation, we assume that as of 2040, only BEVs can be newly registered, which leads to a vehicle stock of about 220,000 BEVs in the near future. Comparable values can be estimated when calculating innovation and imitation coefficients based on the vehicle stock [25] and the new vehicle registrations of electric vehicles [29].
section_name: •

section_content: The third scenario (L) is based on the aim of one million electric vehicles in 2020 [30]. According to [31] and the actual vehicle stock [26], this target is not realistically achievable for 2020, but experts assume that the million level could be reached in 2022 [31]. With the assumptions made for the market volume, we consider this limit as an intermediate target. We further assume that the vehicle stock is increasing exponentially up to that limit, resulting in a vehicle stock of 310,000 BEVs in the near future. Table 2 shows the vehicle stocks in the three scenarios presented. We base the demand for publicly accessible CIS on the electricity demand of the vehicle stock in each scenario. We calculate this electricity demand considering the number of vehicles in each scenario derived from the bass diffusion models, the load requirements per BEV, and the share of at-home-charging (i. e., non-public charging). 

To calculate the load requirements for BEVs, we consider the mileage as well as the average efficiency. To estimate the efficiency of a diverse vehicle stock, we assign the vehicles to three different classes: small car, compact car, and luxury car (sport cars are also regarded as luxury cars in our study). We calculate a ratio of the segments on the total stock of 0. 28, 0. 57, and 0. 15 respectively (based on [32] ) and also calculate the vehicle stock within each class. Furthermore, we derive average efficiencies for each class (13 kWh/(100 km), 14 kWh/(100 km), and 21 kWh/(100 km) respectively) based on current market data [33] [34] [35] [36] [37] [38] [39] [40] [41]. We assume these ratios to be constant over time. For the annual mileage, we assume a constant value of 13,922 km, regardless of the vehicles' class [42]. 

We estimate the share of public charging based on various studies [43] [44] [45] [46] [47]. Hence, we consider a share of the total electricity provided by the public charging infrastructure to be 30% of the total electricity demand for charging. The total energy required by BEVs can either be charged at home or at a publicly accessible charging infrastructure. In our study, we assume that for both systems, home charging is possible (with 3. 7 kW AC, see Section 2. 1). Since a system comparison is intended, the charging infrastructure required for home charging is not considered. The energy requirements of home charging are considered only to the extent that they influence the required number of publicly accessible charging infrastructure. In the following, we focus on the charging infrastructure in the publicly accessible areas if not stated otherwise. 

To derive the number of publicly accessible charging points, the rate of utilization for a charging point, the efficiency of the charging point, and the number of charging points within a charging station need to be estimated. 

We define the rate of utilization as the ratio of the time a charging point is used to the time a charging point theoretically can be used. For the theoretically usable time, we assume a theoretically possible utilization of 12 h a day and 302 days a year. In addition, we assume that each charging point is directly available to other users as soon as the previous car is fully charged (i. e., no additional time gaps). In our study, the rate of utilization is 10%, which implies that there are about 12 BEVs per charging point for the AC system and 27 BEVs for the DC system. This is within the range of the number of electric vehicles per charging point stated in other studies [48] [49] [50]. 

Data available from manufacturers [51] [52] [53] [54] indicate an efficiency for the charging process from 90% to 95% for their charging stations. Using a conservative estimate, we determine an efficiency of 90%. 

With the given data, we calculate the energy provided by each charging point and combine it with the already determined energy demand. For the amount of charging stations, an average of two charging points per charging station is assumed [55]. The resulting number of charging points and charging stations for the scenarios can be seen in Table 2. The formula for the underlying calculations can be found in Appendix A. Having described the technological systems under investigation and having introduced our scenarios, we will now summarize relevant materials and methods of the LCA that we have conducted to assess the environmental impacts of different charging infrastructures. LCA is a commonly used environmental assessment concept [56]. The structure and methodological aspects of LCA are described in the ISO 14040 and ISO 14044 standards [57, 58]. Each LCA can be sub-divided into four phases: the goal and scope definition, Life Cycle Inventory analysis (LCI), Life Cycle Impact Assessment (LCIA), and interpretation. 

For our assessment, we use Ecoinvent 3. 4 [59] as a database and apply the so-called cut-off method. We incorporate the database into the software openLCA 1. 7. 2 [60].
section_name: •

section_content: The goal of this LCA is to determine and compare the systemic environmental impact of the previously described AC and DC-based charging systems. We distinguish between production, transport, and use phases. Due to a lack of data on the regarding processes, recycling is not considered. The functional unit is a kilowatt hour (kWh) that is facilitated by the publicly accessible charging infrastructure. The components examined can be seen in Figure 1. The assumed lifetime for all components is 10 years [49, 61, 62]. Furthermore, we assume that this lifetime applies to all components so that neither the chargers nor the batteries in the BEVs need to be replaced during the lifetime. In accordance with the common LCA method, we conduct the assessment with scaling to a functional unit (i. e., the provision of one kWh charging energy). We neglect the additional consumption of fuel due to the weight of the chargers (for an estimation of weight-related effects, see e. g., [63] ) and estimate the life cycle inventories to the extend necessary due to the non-availability of data. Furthermore, the assembly of the chargers is not considered in the production phase. The geographical scope of our analysis is Germany; however, there are few indications that the findings significantly differ in other countries as discussed in the introduction section. Further, it is assumed that the rate of utilization is constant over time. 

Modular approaches for chargers are often chosen to provide high flexibility and worldwide network connectivity [54, [64] [65] [66]. On the one hand, this allows for a better use of economies of scale We neglect the additional consumption of fuel due to the weight of the chargers (for an estimation of weight-related effects, see e. g., [63] ) and estimate the life cycle inventories to the extend necessary Energies 2020, 13, 6508 6 of 31 due to the non-availability of data. Furthermore, the assembly of the chargers is not considered in the production phase. The geographical scope of our analysis is Germany; however, there are few indications that the findings significantly differ in other countries as discussed in the introduction section. Further, it is assumed that the rate of utilization is constant over time. 

Modular approaches for chargers are often chosen to provide high flexibility and worldwide network connectivity [54, [64] [65] [66]. On the one hand, this allows for a better use of economies of scale for power electronic components; on the other hand, it reduces the maintenance cost and the total failure times of the charging stations. In addition, the charging infrastructure can be gradually adapted to changing charging requirements. Moreover, the overall efficiency can be enhanced by modularity. Therefore, all systems are based on an interconnection of 3. 7 kW chargers. 

The topologies used for the chargers are mainly based on the work of [67, 68]. Therefore, the main reasons are the possibility of modular connection and the well-documented use of components used. The chargers are unidirectional.
section_name: Goal and Scope

section_content: In the following, we briefly describe the LCI, starting with the production phase of the chargers' components. Eventually, we summarize our inventory assumptions for the transport and use phase. For reasons of brevity, additional assumptions about the components for the LCI can be found in Appendix B (see Tables A1 and A2 ).
section_name: Life Cycle Inventory (LCI)

section_content: The components used for the chargers are based on [68, 69]. Components for which no sufficient data are available are replaced by appropriate components for which the corresponding data are accessible. The main distinction between the 3. 7 kW OBC, the 22 kW OBC, and the 50 kW OfBC is the number of the required components. A general overview of modeled systems in this study can be found in Figure 1. In the following, we present each component separately.
section_name: Production of Components

section_content: Low-pass filters are a frequently used option for limiting high-frequency oscillations and noise emissions. Since LCL filters are often used for chargers with a high charging capacity [70] [71] [72], we use an LCL filter in our study. The dimensioning of the filter and its components depends on the associated rectifier and hence on all downstream components [70, 73, 74]. In our paper, we base the dimensioning of the LCL filter on [72, 75], respectively. The components used in our study can be found in Table 3. The number of components is determined by the performance of the chargers, their electrical connection, and the specifications of the components used. To estimate the environmental impacts of the coils, the Ecoinvent [59] dataset for inductors is used as a fairly good estimate and scaled with the associated mass. The production process of the capacitor is modeled using the Ecoinvent [59] dataset "capacitor, film type, for through-hole mounting".
section_name: • Filter

section_content: As for AC-DC converters, we use rectifiers with a downstream power factor correction stage (PFC-converters). The rectifier bridge is combined with a step-up converter. The components used for modeling the AC-DC converter can be found in Table 4. MOSFETs and diodes are modeled with the material data given by the manufacturers and the Ecoinvent production processes for transistors and diodes. The ceramic capacitor used in [67] is modeled with the mass of the capacitor and the dataset for the production of capacitors for surface-mounting in the Ecoinvent database.
section_name: AC-DC converter

section_content: As for DC-DC converters, a common topology for chargers is the isolated full bridge with phase shifted operation. By adjusting the voltage of the active side, the voltage can be adapted to the state of charge of the battery [82, 83]. The components used for the DC-DC converter can be found in Table 5. The MOSFETs are taken from [67]. The material data are given by the manufacturer. For the production process, we use the Ecoinvent dataset for transistors. For the diodes as well as for the capacitor, the stated components are used instead of the ones from [67] due to the non-availability of data. The material data for the diodes are given by the manufacturer; for the production process, the Ecoinvent dataset for diodes is used. The capacitor is modeled as stated before for the AC-DC converter. The production process is modeled with the Ecoinvent dataset for inductors. 1 The number of components for the 22 kW and 50 kW charger is for each phase. 

The dimensioning of the transformer for galvanic isolation is based on [85]. Elgström and Nordgren [85] dimensioned the transformer for a load of 5. 5 kW, which is a sufficient estimate for our study. The stated transformer can be used for modular connection as well. Based on the information on the core [85, 86] and the turns ratio, we can calculate the amount of ferrite and copper. For the production process, the Ecoinvent [59] dataset for wire drawing is used.
section_name: • DC-DC converter

section_name: •

section_content: To mount the electronic components, a PCB is used. We estimate the size based on the outer dimension of the chargers. Details of the calculations can be found in the appendix. For the mounting of the PCB, we use input and output data from [87]. 

Energies 2020, 13, 6508 8 of 31

We adopt the driver board from [87]. According to Nordelöf and Alatalo [87], the structure of driver boards for three-phase inverters for the automotive sector vary negligibly with the power in a range from 20 to 200 kW. We use one of the stated driver boards for each 3. 7 kW charging unit. The design of the logic board is also based on [87], and it is likewise assumed that one logic board is required for each 3. 7 kW charging unit. We base the material flows and the production processes on [87]. 

We base the dimensioning of the busbar on [87, 88]. The production process is modeled based on [87]. 

• Enclosure of electronic components and heatsink. 

Based on [67, 87, 89], we assume that all electronic components share the same enclosure. According to [90], the majority of enclosures is made of aluminum. The material flows and processes used for the production phase of the enclosure with an untreated surface are based on [87]. 

According to Nordelöf and Alatalo [87], the inverter unit considered can be air-cooled for charging capacities up to 50 kW, whereas higher power needs to be liquid-cooled. According to [91], air cooling can also be used for charging stations with significantly higher charging capacity. Therefore, we model an air-cooled heatsink; the material used is aluminum [87]. Process data are taken from [87].
section_name: Printed circuit board (PCB), driver board, logic board and busbars

section_content: Charging infrastructure

The modeled CIS consists of a mains cable for each charging station, a charging cable for each charging point, and a housing for each charging station. 

We assume that charging stations with up to 100 kW output can be attached to the low-voltage grid [66]. A five-core cable is used as a mains cable with the diameter depending on the power supply. Details of the modeling can be found in the appendix. The length of the mains cable is set to 15 m. 

According to [92, 93], for a charging power up to 22 kW, a charging cable of the type 5G6 + 1 × 0. 5 can be used. The total weight as well as the weight of copper is given in the dataset of [93]. For DC charging, a charging cable with diameter 3 × 16 mm 2 and 3 × 2 × 0. 75 mm 2 is used [94]. To estimate the amount of copper, a cable from [95] with 3 × 16 + 3G2. 5 is selected. The length of the charging cable is set to 4 m [92]. 

For 22 kW, a stand-alone housing made of stainless steel is modeled [96] [97] [98] [99] [100] [101] [102] [103]. For the dimension of the charging stations with two 22 kW charging points, a rounded average of the manufacturers sizes is used [96] [97] [98] [99] [100] [101] [102] [103] [104] [105] [106] [107] [108] [109] [110]. 

The dimension of the charging station with two 50 kW charging points is taken from [111]. As material for the 50 kW charging station, stainless steel or a material mix with stainless steel is used [112, 113]. For simplification, we model a housing out of stainless steel. Both dimensions are shown in Table 6.
section_name: •

section_content: For transportation, the Ecoinvent dataset for the transportation of electronic products is used [114]. The total mass is composed of the mass of the aforementioned components. Since the sites of the charging stations are not further specified, the transport of the enclosure, the mains cable, the charging cable, and the housing are not considered in our assessment. 

The use phase considers the provision of one kWh at the publicly accessible charging point. To estimate the environmental impacts, we consider the low-voltage system from Ecoinvent. The energy mix can be found in Table A1 in Appendix B [115]. 

Energies 2020, 13, 6508 9 of 31
section_name: Transport and Use Phase

section_content: Various characterization models exist for impact assessment. According to [116], CML, ReCiPe, and TRACI represent examples of selectable models. Deviations between the underlying properties of these models can affect the LCIA results [117]. Consequently, information about the used LCIA methodology should be stated. We describe selected methodological aspects subsequently. 

In recent years, the damage-based assessment method ReCiPe 2016 [118] has been increasingly used and is therefore selected for our study. Furthermore, for these LCIA methods, the midpoint and endpoint level of the environmental impacts can be assessed [119]. Endpoint impact indicators describe aggregated impacts on "areas of protection" (e. g., human health and the natural environment) [119, 120]. Midpoint impact categories are located at an intermediate position of environmental impact cause-effect chains and consequently before the endpoint categories [119, 120]. An advantage of midpoint indicators in comparison to endpoint indicators is their scientific robustness [121]. We use the Hierarchist perspective and carry out all evaluations on the midpoint level. With the choice of method, the impact categories, impact indicators, and characterization models defined in the method are simultaneously chosen. For the impact categories, we use the abbreviations shown in Table 7.
section_name: Life Cycle Impact Assessment (LCIA)

section_content: Having described relevant materials and methods, we now show our results of the LCA and the economic analysis.
section_name: Results

section_content: We show our results of the LCA first on a component level and then aggregate to a system level. Then, we scale our results according to our diffusion scenarios. Subsequently, we conduct sensitivity analyses to account for uncertainties in modeling.
section_name: Results and Interpretation of the Life Cycle Impact Assessment (LCIA)

section_content: In the following, the component level is evaluated to identify individual components with high optimization potential within the power electronics and the charging infrastructure. This implies that the environmental impacts specified below apply to one provided kWh by one charger or one public charging station or one publicly accessible charging point, respectively.
section_name: Component-Based Results

section_content: We identify the filter to be a main polluter for 3. 7 kW chargers as well as for 22 kW chargers. For 50 kW chargers, the filter as well as the DC-DC converter are main polluters. For all filters, the inverter-side coils are the main contributors to pollution. In the DC-DC converter, the coils and transformers are the components with a major influence in all impact categories. The transformers outvalue the coils when it comes to mineral resource depletion, which can be explained with the ferrite used for the core. For the AC-DC converter, the coils are main polluters as well, followed by diodes, MOSFETs, and capacitors. The percentage share of the components can be found in Figure 2, which is exemplary for the 22 kW charger. See Table A3 in Appendix C for more detailed results. 

Energies 2020, 13 We identify the filter to be a main polluter for 3. 7 kW chargers as well as for 22 kW chargers. For 50 kW chargers, the filter as well as the DC-DC converter are main polluters. For all filters, the inverter-side coils are the main contributors to pollution. In the DC-DC converter, the coils and transformers are the components with a major influence in all impact categories. The transformers outvalue the coils when it comes to mineral resource depletion, which can be explained with the ferrite used for the core. For the AC-DC converter, the coils are main polluters as well, followed by diodes, MOSFETs, and capacitors. The percentage share of the components can be found in Figure 2, which is exemplary for the 22 kW charger. See Table A3 in Appendix C for more detailed results. 

When considering the impact of power electronics and the enclosure, it turns out that for the 22 kW charger, the power electronics account for more than 50% of the environmental impacts for all impact categories. The enclosure has the main impact for all chargers when it comes to climate change and the least when considering mineral resource depletion.
section_name: • Power electronics

section_content: As for the CIS, we consider the mains cable, the charging cable, and the housing. For the 22 kW CIS, the mains cable is the main emitter in all impact categories. The mains cable has the highest impact in 13 out of 18 impact categories (except agricultural land occupation, climate change, fossil resource depletion, ionizing radiation, and ozone depletion) for the 50 kW charging station. When comparing the mains cable of the 22 kW CIS and the 50 kW CIS, the mains cable for the 50 kW charging station has between 72% (fossil resource depletion) and 90% (mineral resource depletion) higher impacts than the mains cable for the 22 kW charging station. Considering the charging cable, the charging cable for the 50 kW charging station causes between 39% (fossil resource depletion) and 146% (mineral resource depletion) higher impacts than the charging cable for the 22 kW charging station. For the 22 kW charging station, the charging cable causes less than 3. 2% in all impact When considering the impact of power electronics and the enclosure, it turns out that for the 22 kW charger, the power electronics account for more than 50% of the environmental impacts for all impact categories. The enclosure has the main impact for all chargers when it comes to climate change and the least when considering mineral resource depletion.
section_name:  Charging infrastructure (CIS)

section_content: Charging infrastructure (CIS)

As for the CIS, we consider the mains cable, the charging cable, and the housing. For the 22 kW CIS, the mains cable is the main emitter in all impact categories. The mains cable has the highest impact in 13 out of 18 impact categories (except agricultural land occupation, climate change, fossil resource depletion, ionizing radiation, and ozone depletion) for the 50 kW charging station. When comparing the mains cable of the 22 kW CIS and the 50 kW CIS, the mains cable for the 50 kW charging station has between 72% (fossil resource depletion) and 90% (mineral resource depletion) higher impacts than the mains cable for the 22 kW charging station. Considering the charging cable, the charging cable for the 50 kW charging station causes between 39% (fossil resource depletion) and 146% (mineral resource depletion) higher impacts than the charging cable for the 22 kW charging station. For the 22 kW charging station, the charging cable causes less than 3. 2% in all impact categories. For the 50 kW charging station, the impact of the charging cable is below 4% in all impact categories. The housing of the 50 kW charging station causes about three times higher impacts than the 22 kW charging station for all impact categories. For both charging stations, the housing has the highest impact in the impact category climate change.
section_name: •

section_content: The following results refer to a system level. The scaling of the components is shown in Table 1.
section_name: System-Based Results

section_content: For the DC system, the total amount of 3. 7 kW OBCs (scales with the number of vehicles) leads to higher environmental impacts (more than 70% for all impact categories) than the sum of the 50 kW chargers (scales with the number of charging points). The relative impact of the 50 kW chargers is highest for human toxicity (about 28%). Concerning global warming, the 3. 7 kW chargers account for about 80% of the emitted CO 2 -eq. (0. 07 kg CO 2 -eq. /kWh).
section_name: • Chargers

section_content: Charging infrastructure (CIS)

When comparing the environmental impacts of the CIS on a system base, the AC system has less environmental impacts in 10 out of 18 impact categories when compared to the CIS of the DC system. We find the most significant difference (percentage wise) to be present in climate change with additional emissions of 0. 7 • 10 -3 kg CO 2 -eq. per kWh when the DC system is used. The environmental impacts of the charging infrastructure for the AC system and the DC system can be found in Table A4 in Appendix C. 

When comparing the environmental impacts of the total number of chargers and the CIS, chargers account for over 90% of the environmental impacts for all impact categories in the AC system. For the DC system, the CIS has a more significant environmental impact (percentage wise) than in the AC-based system. The most significant impact of the CIS in the DC system can be seen in human toxicity (about 25% or 0. 05 kg 1,4-DCB-eq. /kWh). The transport only accounts for less than 0. 3% of the emissions in all impact categories; therefore, it is neglected in further examinations.
section_name: •

section_content: Charging infrastructure, chargers, transport, and use phase When summing up the environmental impacts of the production (chargers as well as charging infrastructure) and comparing them with the environmental impacts of the use phase (energy provision), we find that the use phase is responsible for more than 50% of the environmental impacts in 12 impact categories for the AC system. Only mineral resource depletion, photochemical oxidant formation, natural land transformation, particulate matter formation, terrestrial ecotoxicity, and urban land occupation predominate in the production phase. When considering the DC system, solely mineral resource depletion is dominant during production, while all other environmental impacts are mainly emitted during the use phase. 

Referring to global change in the AC system, only about 30% of CO 2 -eq. are emitted during production; while in the DC system, it is less than 12%. Due to the scaling to one kWh (i. e., the functional unit) and the same charging efficiency for all chargers, the same total amount of emissions is emitted during the use phase in both systems, which also means that changes in the energy mix have the same impact on the use phase for both systems. 

When comparing the overall environmental impacts of the two systems (production, transport, and use), a reduction of environmental impacts in all 18 impact categories is achieved by the DC system. Figure 3 shows the results-with the environmental impacts of the AC system scaling to 100%. We observe the most significant differences in percentage terms in mineral resource depletion (68. 11%), photochemical oxidant formation (48. 10%), and natural land transformation (44. 77%). The most significant absolute changes can be observed in the impact categories human toxicity (0. 36 kg 1,4-DCB-eq. /kWh), mineral resource depletion (0. 19 kg Fe/kWh), and climate change (0. 19 kg CO 2 -eq. /kWh). For mineral resource depletion (see Figure 4a ), power electronics have the most significant impact (≈68% and ≈90%, respectively). It was shown before that mainly the DC-DC converter and the filter contribute to that impact. Within the converter and the filter, the coils constitute the main demand for mineral resources. For natural land transformation (see Figure 4b ) in the AC-based system, the production of power electronics (mainly the filter) could be identified as main contributors (≈55%) while for the DC system, the use phase is the main contributor. Considering photochemical oxidant formation (see Figure 4c ), in the AC system, power electronics (filter and DC-DC converter) are the main contributors, while it is the use phase in the DC system. For mineral resource depletion (see Figure 4a ), power electronics have the most significant impact (≈68% and ≈90%, respectively). It was shown before that mainly the DC-DC converter and the filter contribute to that impact. Within the converter and the filter, the coils constitute the main demand for mineral resources. For natural land transformation (see Figure 4b ) in the AC-based system, the production of power electronics (mainly the filter) could be identified as main contributors (≈55%) while for the DC system, the use phase is the main contributor. Considering photochemical oxidant formation (see Figure 4c ), in the AC system, power electronics (filter and DC-DC converter) are the main contributors, while it is the use phase in the DC system. 

The most significant absolute changes were observed in the impact categories human toxicity (0. 36 kg 1,4-DCB-eq. /kWh), mineral resource depletion (0. 19 kg Fe/kWh), and climate change (0. 19 kg CO 2 -eq. /kWh). For human toxicity (see Figure 5a ), the use phase has the highest impact followed by power electronics. Within the power electronics for the 22 kW charger, the main contributor is the DC-DC converter followed by the filter and the logic board. For climate change (see Figure 5b ), the main source of environmental impacts is the use phase. Within the production of the power electronics, it is mainly the filter that contributes to climate change for both the 22 kW and the 50 kW charger. The most significant absolute changes were observed in the impact categories human toxicity (0. 36 kg 1,4-DCB-eq. /kWh), mineral resource depletion (0. 19 kg Fe/kWh), and climate change (0. 19 kg CO2-eq. /kWh). For human toxicity (see Figure 5a ), the use phase has the highest impact followed by power electronics. Within the power electronics for the 22 kW charger, the main contributor is the DC-DC converter followed by the filter and the logic board. For climate change (see Figure 5b ), the main source of environmental impacts is the use phase. Within the production of the power electronics, it is mainly the filter that contributes to climate change for both the 22 kW and the 50 kW charger.
section_name: •

section_content: In a next step, we apply our results to the diffusion scenarios that we have introduced in Section 2. 2. Therefore, the analysis is no longer carried out for one kWh of charging electricity (i. e., the functional unit), but rather based on the stock of BEVs and the regarding charging requirements per scenario. The absolute environmental impacts for the scenarios can be found in Table A2 in Appendix B. Table 8 describes the absolute reductions of environmental impacts in selected impact categories that could be achieved by implementing the DC system instead of the AC system with considering a Energies 2020, 13, 6508 14 of 31
section_name: Scenario-Based Results

section_content: In a next step, we apply our results to the diffusion scenarios that we have introduced in Section 2. 2. Therefore, the analysis is no longer carried out for one kWh of charging electricity (i. e., the functional unit), but rather based on the stock of BEVs and the regarding charging requirements per scenario. The absolute environmental impacts for the scenarios can be found in Table A2 in Appendix B. Table 8 describes the absolute reductions of environmental impacts in selected impact categories that could be achieved by implementing the DC system instead of the AC system with considering a lifetime of 10 years for all components. In the impact category, climate change of about 20, 25, and 35 mn. kg CO 2 -eq. yearly can be saved when implementing the DC system instead of the AC system. That would represent approximately 0. 012%, 0. 016%, and 0. 022% of current annual greenhouse gas emissions in the transport sector in Germany [7]. The analysis also indicates that the potential for reductions increases as the number of BEVs increases.
section_name: Scenario-Based Results

section_content: To account for data uncertainties in modeling, we conduct sensitivity analyses. Therefore, we vary the emission intensity of the production of the power electronics. Additionally, we vary the average utilization of the charging points as well as the efficiency of the charging points and the ratio of home charging (i. e., non-public charging, see modeling in Section 2. 2). We provide an overview of our parameter variations in Table 9. The investigated parameters represent those with the highest effect on our results. We conduct the analyses for all 18 impact categories and exemplify it for significant impact categories. The variation in the environmental impact of power electronics production results in greater environmental impacts in the AC system even for the most unfavorable combination for the DC system (DC system: 120%; AC system: 80%) for all impact categories. As the power electronics have the main impact in the overall systems in mineral resource depletion (90% in the AC system and 68% in the DC system), natural land transformation (56% in the AC system and 25% in the DC system), and photochemical oxidant building (60% in the AC system and 29% in the DC system), the result of the sensitivity analyses is shown to be exemplary for those impact categories (Figure 6a-c ). Additionally, the result for climate change is shown in Figure 6d. This suggests that even with greater uncertainties in the environmental impact of power electronics, the DC system has lower environmental impacts than the AC system in our model. When varying the degree of utilization, the most considerable changes on a percentage basis are in human toxicity, mineral resource depletion, and terrestrial ecotoxicity (see Figure 7a-c ). Again, Figure 7d shows the result for climate change. When varying the degree of utilization, the most considerable changes on a percentage basis are in human toxicity, mineral resource depletion, and terrestrial ecotoxicity (see Figure 7a-c ). Again, Figure 7d shows the result for climate change. The efficiency of the charging process can vary considerably, although charging stations with higher charging powers usually have a higher efficiency. When comparing the most unfavorable combination for the DC system (DC system: 80%; AC system: 100%), the AC system has less environmental impacts in the impact categories agricultural land occupation, freshwater ecotoxicity, ionizing radiation, and water depletion. The resulting sensitivities for the impact categories are shown in Figure 8a-d. From our results, we can conclude that although there are cases where the AC system causes less emissions than the DC system in the above-mentioned impact categories, the mean and median of the DC system are significantly below the mean and median of the AC system in all critical impact categories. The efficiency of the charging process can vary considerably, although charging stations with higher charging powers usually have a higher efficiency. When comparing the most unfavorable combination for the DC system (DC system: 80%; AC system: 100%), the AC system has less environmental impacts in the impact categories agricultural land occupation, freshwater ecotoxicity, ionizing radiation, and water depletion. The resulting sensitivities for the impact categories are shown in Figure 8a-d. From our results, we can conclude that although there are cases where the AC system causes less emissions than the DC system in the above-mentioned impact categories, the mean and median of the DC system are significantly below the mean and median of the AC system in all critical impact categories. 

Energies 2020, 13 When varying the ratio of home charging (i. e., non-public charging and therefore the number of publicly accessible charging stations, see Section 2. 1) and evaluating the DC system's most unfavorable combination (DC system: 80%; AC system: 60%), the DC-based system has less environmental impacts in all impact categories, even though the DC system has more charging points than the AC system in this constellation. The results are shown in Figure 9, which are exemplary for the most significant changes (on a percentage basis) (Figure 9a-c ) as well as for climate change (Figure 8d ). However, it should be noted that the total energy demand does not change if the proportion of home charging is increased. Since the energy used for home charging is not included in the modeling, there are large variations in the considered impact categories. This effect would decrease if the energy required for home charging was included. When varying the ratio of home charging (i. e., non-public charging and therefore the number of publicly accessible charging stations, see Section 2. 1) and evaluating the DC system's most unfavorable combination (DC system: 80%; AC system: 60%), the DC-based system has less environmental impacts in all impact categories, even though the DC system has more charging points than the AC system in this constellation. The results are shown in Figure 9, which are exemplary for the most significant changes (on a percentage basis) (Figure 9a-c ) as well as for climate change (Figure 8d ). However, it should be noted that the total energy demand does not change if the proportion of home charging is increased. Since the energy used for home charging is not included in the modeling, there are large variations in the considered impact categories. This effect would decrease if the energy required for home charging was included. 

Summing up, the sensitivity analyses showed some combinations for which the DC system has more environmental impacts in some impact categories (i. e., agricultural land occupation, freshwater ecotoxicity, ionizing radiation, and water depletion; see Figure 8 ). Nevertheless, the overall finding, that the DC system has less environmental impacts than the AC system in the modeled system, seems to be consistent, as this constellation only represents rather unlikely parameter combinations. Summing up, the sensitivity analyses showed some combinations for which the DC system has more environmental impacts in some impact categories (i. e., agricultural land occupation, freshwater ecotoxicity, ionizing radiation, and water depletion; see Figure 8 ). Nevertheless, the overall finding, that the DC system has less environmental impacts than the AC system in the modeled system, seems to be consistent, as this constellation only represents rather unlikely parameter combinations.
section_name: Sensitivity Analyses

section_content: We conduct the economic analysis and distinguish between CIS and charging devices. The considered cost components are shown in Table 10. All estimates are based on [61, 122, 123]. The costs for the CIS and the chargers are annualized.
section_name: Economic Analysis

section_content: We conduct the economic analysis and distinguish between CIS and charging devices. The considered cost components are shown in Table 10. All estimates are based on [61, 122, 123]. The costs for the CIS and the chargers are annualized. We calculate the cost for the CIS for all three diffusion scenarios. Figure 10 shows our results. Despite the fewer charging stations in the DC system, the higher costs of the charging stations cannot be compensated. The system costs for the CIS in the DC system are about 180% higher than the system costs in the AC system. 

Energies 2020, 13, x; doi: www. mdpi. com/journal/energies be compensated. The system costs for the CIS in the DC system are about 180% higher than the system costs in the AC system. For the OBC, the cost estimation is based on Mathieu [124], who states about 250 EUR for a 3. 7 kW charger. Due to the modular design in our paper, the cost for the 22 kW chargers results in 1500 EUR. The costs for the OBCs in the scenarios are shown in Figure 10. 

The OBCs have a significant impact for the AC system. About 70% of the total cost for the AC system arise from the OBCs, while in the DC system, the OBCs are only about 13% of the total cost. Thus, in total, the AC system becomes more expensive than the DC system. From a system point of view, in our scenarios, 4. 2 mn., 5 mn. and 8. 5 mn. euros can be saved annually with the DC-based charging infrastructure compared to the AC-based system. The analysis also indicates that the potential for savings increases with the number of BEVs.
section_name: Economic Analysis

section_content: In our study, we analyzed and compared the environmental impacts of different charging concepts for electric vehicles. Two systems were considered, which essentially differ in the position of the chargers. When charging with alternating current (AC), an on-board charger is used. In our AC system, a charging power of 22 kW is considered for the publicly accessible charging infrastructure, and home charging with 3. 7 kW can be conducted without any additional components. Charging at higher power levels requires an off-board charger. In the DC system, a For the OBC, the cost estimation is based on Mathieu [124], who states about 250 EUR for a 3. 7 kW charger. Due to the modular design in our paper, the cost for the 22 kW chargers results in 1500 EUR. The costs for the OBCs in the scenarios are shown in Figure 10. 

The OBCs have a significant impact for the AC system. About 70% of the total cost for the AC system arise from the OBCs, while in the DC system, the OBCs are only about 13% of the total cost. Thus, in total, the AC system becomes more expensive than the DC system. From a system point of view, in our scenarios, 4. 2 mn., 5 mn. and 8. 5 mn. euros can be saved annually with the DC-based charging infrastructure compared to the AC-based system. The analysis also indicates that the potential for savings increases with the number of BEVs.
section_name: Conclusions and Outlook

section_content: In our study, we analyzed and compared the environmental impacts of different charging concepts for electric vehicles. Two systems were considered, which essentially differ in the position of the chargers. When charging with alternating current (AC), an on-board charger is used. In our AC system, a charging power of 22 kW is considered for the publicly accessible charging infrastructure, and home charging with 3. 7 kW can be conducted without any additional components. Charging at higher power levels requires an off-board charger. In the DC system, a charging power of 50 kW is assumed. Additionally, a 3. 7 kW on-board charger is designed to allow for AC charging at home (3. 7 kW). In our modeled systems, publicly accessible infrastructure rather solely supports AC charging (22 kW) or DC charging (50 kW). The calculation of the required charging infrastructure is based on the total energy demand for charging in the publicly accessible area. We defined three diffusion scenarios to model the near-future stock of BEVs in Germany and the required amount of charging infrastructure. 

According to the goal of our study, we evaluated the environmental impacts of the systems by conducting an LCA. Our results show that the DC charging system causes less environmental impacts than the AC system in all impact categories. Even though the use phase has a large impact on the environmental analysis, it has the same impact for both systems when scaling to 1 kWh due to the model parameters. For the production, we showed that-on a component level-chargers are the main contributor in both systems. In the DC system, the sum of 3. 7 kW chargers has a greater impact than the sum of the 50 kW chargers. Within the chargers, we identified the filters as main polluters for the 3. 7 kW and the 22 kW chargers. For 50 kW chargers, the filter and the DC-DC converter cause the most environmental impacts. For all filters, the inverter-side coils are the main polluters. In the DC-DC converter, the coils and transformers are the components with a major influence in all impact categories. When assigning the results to our scenarios, for global warming, annual emission reductions of 20 mn., 25 mn., and 35 mn. kg CO 2 -eq. could be achieved when the DC system is used instead of the AC system, which represent approximately 0. 012%, 0. 016%, and 0. 022% of current annual greenhouse gas emissions in the German transport sector [7]. 

The main reason for the differences in the two systems is the scaling. While in the AC system each vehicle is equipped with a 22 kW charger (the number of chargers and the corresponding power electronics scales with the number of vehicles (see Table 1 ), in the DC system, the users of electric vehicles share the chargers and the corresponding power electronics in publicly accessible areas (the 50 kW chargers scale with the number of charging stations (see Table 1 )). 

Our sensitivity analyses confirmed the advantages of the DC system and showed the robustness of the results. Even in cases for the most unfavorable combination for the DC system, it causes less environmental impacts than the AC system. 

For our economic analysis, we calculated the cost on a German-national level. Even though the DC charging infrastructure causes significantly higher cost than the AC charging infrastructure, this becomes less important when the costs of the OBCs are also considered. In our scenarios, annual savings of 4. 2 mn., 5. 4 mn., and 8. 5 mn. euros are possible when the DC system is used instead of the AC system. The reductions of environmental impacts and the cost savings both scale with the stock of BEVs in our model. 

All findings gained should be considered within the model boundaries. First, we want to mention that even though the Ecoinvent database is commonly used, some generic processes may have changed over time, so there may be some shifts of the environmental impacts. In addition, the database is often based on processes from the European area, which should be taken into account when transferring the results to other countries, although it cannot necessarily be assumed that the processes and environmental impacts differ significantly. Furthermore, our study is only valid for the modeled components. If different or additional components are used, e. g., if the charging power is changed, the resulting environmental impacts of these components must be considered separately. In addition, the density of the publicly available charging infrastructure is not explicitly investigated. Although the sensitivity analysis of the utilization shows that even when the DC system has more charging points than the AC system it causes less environmental impacts than the AC system, this aspect would need to be investigated further. Another assumption made is that the energy mix stays constant during the day. As the CO 2 intensity of the energy supply differs intraday, considering the charging behavior of users within the systems is an interesting supplement as well. Nevertheless, the study provides a systems comparison of AC and DC-based charging and gives an overview of the components that have a relevant environmental impact and that may need to be modeled in more detail in future considerations. 

Based on environmental as well as economic results, our study shows that DC charging offers both economic saving and environmental reduction potentials. The advantages of the DC system scale with the number of electric vehicles, so it can be assumed that the findings will become more relevant as the number of BEVs increases. With the current distribution of charging solutions in Germany, on-board charging dominates, while off-board charging accounts for about 7% of all public charging points. The on-board charging capacity of the newly offered vehicles seems to settle at a level of 11 kW. In order to achieve higher charging performance, off-board charging will be increasingly used.
section_name: Conclusions and Outlook

section_content: Printed circuit board (PCB), driver board, logic board, and busbars

For the size estimation of the size of the PCB, we estimate the outer dimension of the chargers. Schmenger et al. [68] state the volumes of the modular chargers for different charging powers. Based on the assumption that the 50 kW charger has the same power density as the 22 kW charger, we estimate the volume for the 50 kW charger. The ratio of width and height is based on [89]. We assume that the ratio remains constant over power. Based on the model from [89], we assume that the area of the PCB is 30% of the area of the charger. 

As stated above, we base the dimensioning of the busbar on [87, 88]. As stated by Mersen [88], an ampacity of 5 A/mm 2 is considered and a 5% security surcharge is obeyed for each additional conductor. The minimum cross-sectional area is based on [87]. The maximum current considered originates from [67, 68]. We estimate the maximum current based on the modularity of the charging unit. For the AC busbars, a quantity of three trace pitches can be assumed [87]. For the DC busbars, two trace pitches are assumed. We estimate the length of the busbars based on the outer dimensions of the charger [67]. The production process is modeled based on [87]. The surface of the busbars is galvanically nickel-plated. With the assumption of a thickness of 1 mm for the bus bars, a thickness of 20 µM for nickel-plating [87] and the density of 8900 kg/m 3 for nickel the material flow and process data are based on [87].
section_name: •

section_content: To calculate the material flows of the enclosure for electronic components, the dimensions of the heatsink need to be estimated in a first step. The heatsink for the electronic devices shown in [89] is liquid-cooled. Based on [87], a thickness of 2. 5 cm can be assumed. Under the assumption that the remaining space is used by electronic devices, we calculate the height of the enclosure for the electronic components from the dimensions of the charging unit and the height of the heat sink. The heat sink composes the base plate of the charging unit and is modeled separately. The material flows and processes used for the production phase of the enclosure with an untreated surface are based on [87]. 

The size estimations for our air-cooled heatsink are based on the assumption of a forced cooling with an airflow of at least 7 m/s [87]. We do not model the fan. We determine the mass of the air-cooled heatsink on the basis of a standard heatsink [126]. In our estimations, the size of the heat sink matches the base area of the charging unit. With the given ratio of weight and length of the heatsink [126], we estimate the mass of aluminum. For surface refinement, the surface area of the heatsink is anodized [87]. We estimate the surface to be anodized by taking the number of lamellas from [126] without considering the changing number of lamellas with the changing width. Therefore, each lamella has two sides to be anodized. The side of the heatsink that forms the bottom surface of the housing is not treated. With the anodizing surface calculated, accordingly, the further process data is taken from [87].
section_name: Enclosure of electronic components and heatsink

section_content: Charging infrastructure (CIS)

Based on [127] for a charging station with two charging points at 22 kW, we select the mains cable by [128] (Type NYY-J 5 × 50 SW) and assume that the difference of the total weight to the weight of copper is caused by insulation. Due to the fact that the material for the insulation is not differentiated any further in the dataset of the manufacturer, we base our estimation of the composition of the insulation and the processes needed for production on the Ecoinvent dataset "cable connector for computer, without plugs" [125]. For 50 kW charging power, a cross-section of the mains cable of 75 mm 2 or 90 mm 2 is used [129]. Due to the non-availability of data, we use a 95 mm 2 cable for modeling [128] (Type NYY-J 5 × 95 SW). We calculate the quantity of insulation as described above. 

For the charging cable, the insulation is estimated as mentioned above as the difference between the weight of copper and the total weight. The materials used for insulation as well as the production processes are based on the aforementioned dataset in Ecoinvent. 

Regarding the housing, the most common stainless steel alloy (steel of grade 304 and 304L which consists of 18% chrome and 8% nickel and has a density of 8000 kg/m 3 [130] ) is used. The wall thickness is set to 2 mm [131]. For its production, the Ecoinvent dataset for sheet rolling is used. According to [96], the stainless steel is powder-coated. The related process is taken from Ecoinvent. Reference: for detailed information, please refer to [115]. 

Table A2. Environmental impacts of the AC system and the DC system for modeled scenarios considering a lifetime of 10 years.
section_name: •

section_name: Impact Category

section_content: Funding: L. N., B. J. M., R. W. D. D. and A. P. received funding by the Federal Ministry of Education and Research (BMBF) and the Ministry of Culture and Science of the German State of North Rhine-Westphalia (MKW) under the Excellence Strategy of the Federal Government and the Länder (grant ID: ( DE-82 ) EXS-SF-OPSF560 ). J. C. K. and W. K. gratefully acknowledge funding of the center of excellence "Virtual Institute-Power to Gas and Heat" ( EFRE-0400151 ) by the " Operational Program for the promotion of investments in growth and employment for North Rhine-Westphalia from the European fund for regional development" (OP EFRE NRW) through the Ministry of Economic Affairs, Innovation, Digitalization and Energy of the State of North Rhine-Westphalia.

section_name: Conflicts of Interest:

section_content: Author Contributions: Conceptualization, M. K., L. N., B. J. M., J. C. K., W. K., R. W. D. D. and A. P. ; Data curation, M. K. ; Formal analysis, M. K. ; Methodology, M. K., L. N., B. J. M., J. C. K., W. K., R. W. D. D. and A. P. ; Resources, L. N., B. J. M., J. C. K., W. K., R. W. D. D. and A. P. ; Software, M. K. ; Supervision, L. N., B. J. M., J. C. K., W. K., R. W. D. D. and A. P. ; Validation, L. N., B. J. M., J. C. K., W. K., R. W. D. D. and A. P. ; Visualization, M. K. ; Writing-original draft, M. K. ; Writing-review and editing, M. K., L. N., B. J. M., J. C. K. and A. P. All authors have read and agreed to the published version of the manuscript.

section_content: The authors declare no conflict of interest.
section_name: Conflicts of Interest:

section_content: The total number of charging stations is calculated as follows: In the following, we provide a more detailed description of the components modeled in Section 2. 3. 2. The structure of the background information is similar to the structure in in the Sub-Section Production of Components.
section_name: Appendix A. Background Information to Section 2.2

section_content: For the calculations, we use a maximum current ripple of 15% [70]. For the design of the filter capacity, we assume that the maximum change in the power factor perceived by the grid is 5%. The desired attenuation is set to 20%, the switching frequency of 200 kHz and the DC voltage result from [68, 69], respectively. Based on the specified parameters, we select electronic components that sufficiently fulfill the characteristics, are available on the market, and for which material data are available. The components used in our study can be found in Table 3.
section_name: • Filter

section_content: Even though the capacitors for surface-mounting in the Ecoinvent database are not specified in [125], the dataset shows a ratio of 40% ceramics and is therefore considered as the best available dataset for ceramic capacitors. As an estimate for the mass of the capacitor, a dataset with mass specification from Murata is used [80]. The coil EELP 58 is used instead of EELP 54 [81]. The mass of the core is given in the manufacturers' dataset. For the windings, we assume that 60% of the cores' air space is filled with wire. With the density of copper (8920 kg/m 3 ), the mass of copper for the windings is estimated. The production process is modeled with the Ecoinvent dataset for inductors.
section_name: • AC-DC Converter

section_content: For the coil core, EELP64 is used. The amount of copper is calculated as shown for the AC-DC converter.
section_name: • DC-DC Converter