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Article

Agricultural LCA for Food Oil of Winter Rapeseed, Sunflower, and Hemp, Based on Czech Standard Cultivation Practices

by
Jaroslav Bernas
1,*,
Tereza Bernasová
2,
Václav Nedbal
2 and
Reinhard W. Neugschwandtner
3
1
Department of Agroecosystems, Faculty of Agriculture, University of South Bohemia, Studentska 1668, 37005 Ceske Budejovice, Czech Republic
2
Department of Applied Ecology, Faculty of Agriculture, University of South Bohemia, Studentska 1668, 37005 Ceske Budejovice, Czech Republic
3
Department of Crop Sciences, Institute of Agronomy, University of Natural Resources and Life Sciences Vienna (BOKU), 3430 Tulln, Austria
*
Author to whom correspondence should be addressed.
Agronomy 2021, 11(11), 2301; https://0-doi-org.brum.beds.ac.uk/10.3390/agronomy11112301
Submission received: 21 October 2021 / Revised: 9 November 2021 / Accepted: 11 November 2021 / Published: 13 November 2021
(This article belongs to the Section Farming Sustainability)
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Abstract

:
The demand for food vegetable oil is rising and this trend is reflected in the agricultural sector of the Czech Republic. The traditional oil crops of the Czech Republic are winter rapeseed and sunflower. These oil crops have high demands on energy inputs, for example, in the form of land preparation and chemical protection. At the same time, they are characterized by high food oil production and oiliness. Moreover, marginal oils crops, such as hemp, are also gaining prominence. This work aimed to evaluate the environmental impacts associated with the cultivation of winter rapeseed and sunflowers based on standard cultivation practices typical of the conditions of the Czech Republic. For comparison, an intensive cultivation strategy for hemp was modelled, also corresponding to the conditions of the Czech Republic. This study assessed the environmental impact of traditional oil crops from the agricultural Life Cycle Assessment (LCA) perspective. The system boundaries included all the processes from the cradle to the farm gate. Mass-based (volume of food oil) and area-based (land demand for generating the same volume of food oil) functional units were employed. The results cover nine impact categories related to the agricultural LCA. ReCiPe Midpoint (H) characterization and normalization models were used for the data expression. Hemp is a plant with generally low demands on the inputs of the growing cycle but generally has a low oil production, which affects the character of the results relating to the goal and scope definition of the study. Hemp food oil thus generated a higher environmental impact per unit of production and area compared to sunflower and rapeseed food oil.

1. Introduction

The food sector is one of the major consumers of food oil, and the demand for food vegetable oil has been increasing for a long time [1]. The world’s most cultivated oil crops have long been soybeans, rapeseed, cottonseed, peanuts, sunflowers, palm kernels, and coconuts. European vegetable oil consumption is based mainly on rapeseed, palm oil, soybeans, and sunflowers [2]. In the Czech Republic, winter rapeseed, poppy, sunflower, soybean, mustard, and linseed have traditionally had the highest share in the area under oil crops [3]. The Czech Republic has 2,958,603 ha of arable land; winter rapeseed was grown on approximately 380,000 ha (12.5%) and sunflowers on about 15,000 ha (0.5%) in recent years [2]. Nearly half of winter rapeseed oil production is for food purposes. Hemp, which has good potential in food oil production [4,5], is also beginning to appear increasingly (at about 600 ha) on arable land in the Czech Republic [3].
All agricultural activity is more or less linked to the impact on the environment [6]. The intensity of these impacts is also related to the intensity of agricultural production itself. In particular, oil crops, such as rapeseed, are among the crops that generally have high demands in terms of treatment and care [7]. These demands are then reflected in the impacts on the environment and its individual components [8,9]. Sustainable development, sustainable production, and consumption in the agri-food sector are key issues stimulating the creation of many international activities and strategies to reduce environmental impacts and seek sustainable production routes [10]. Due to the wide range of possible impacts on the environment and their diversity, it is not easy to evaluate the complex effects of the agricultural system with one method. There are various methods for assessing one or more indicators that determine the level of a particular impact. They can be quantified, for example, through the agricultural Life Cycle Assessment (LCA) method [11] and can thus point out possible options that could lead to the mitigation of these impacts [12].
Thanks to LCA, it is also possible to carry out a comparative study, which can help find a suitable alternative or point to new possibilities in general crop production and oil crops production. Agricultural LCA aims for a comprehensive assessment of the environmental profile of the product system and is one of the most holistically applicable methods. Agricultural LCA is the widely accepted methodology for assessing the potential environmental impacts of agri-food chains and agricultural production systems. It is an analytical method that assesses the environmental impacts of products, services, technologies and human products and organizations in general [13]. In recent years, the number of studies evaluating the impact of agricultural products using the LCA method has increased. Comparative studies are often used to compare the environmental sustainability of products from different agricultural production systems [12]. Before the implementation of a potential sustainable farming system, scientists and the decision-makers need sufficient information about the positives and negatives of the production system with regard to productivity and performance. The LCA method provides a suitable assessment tool that meets the requirement of a comprehensive assessment of the environmental impacts of different production systems [12]. These outputs can then help implement concepts that correspond to the strategies of the common agricultural policy (CAP) and the European Green Deal [14]. However, for the conditions of the Czech Republic, such a model based on an LCA of winter rapeseed oil (sunflower oil and hemp oil, also) has not yet been implemented, although winter rapeseed is one of the dominant crops on arable land. Whereas rapeseed cultivation can bring more biological diversity to the landscape, as reported for Sweden which has a share of rapeseed on arable land of about 4% [15], the Czech Republic has a share of 14%—the highest in the EU [16].
This comparative LCA study aims to quantify the environmental impact associated with conventional winter rapeseed and sunflower food oil production, as the most widely represented oil crops in the Czech Republic, and to compare them with conventional hemp cultivation, which has in recent years gained great popularity in many agricultural sectors [17]. The attribution approach, the mass allocation principle, the characterization model, and the normalization model for data interpretation were chosen for this study. The functional unit related to the yield (volume of food oil yield) and the functional unit related to the area equivalent to the area needed to gain the same yield (volume of food oil) are used for data interpretation. This study reviews the environmental impact of rapeseed, sunflower, and hemp food oil production from the perspective of Czech standard cultivation practices. The results point to the impacts of individual inputs on the growing cycles and farming strategies, respectively, and allow for comparison of the two dominant oil crops (winter rapeseed and sunflower) and one minor alternative oil crop with the promised environmental potential. This paper will expand knowledge concerning winter rapeseed, sunflower, and hemp production with respect to environmental issues, and bring a new perspective to agronomy policy design.

2. Materials and Methods

2.1. Goal and Scope Definition

This study aims to quantify the environmental impacts of winter rapeseed oil, sunflower oil, and hemp oil by using the agricultural LCA. A functional unit (FU) related to production (1 m3 of food oil) and area unit (land demand for generating the same yield of food oil) was chosen for this study. The system boundaries include all the processes “from cradle to farm gate”. Data geographically related to central Europe and the Czech Republic were used. As in a study based on agricultural LCA [18,19], agrotechnological operations were also incorporated into the model system: from pre-seeding preparation, through harvesting of the main product, to the transport of farming machinery, the production and use of crop-protecting agents, the production and use of fertilizers, the harvest, and transportation of the main product from the harvest site. Land-use changes were taken into account. Infrastructure processes were part of database inputs. Manure production and management have not been included. Cow manure was considered to be a residual product of the animal production systems, so emissions from the animal production system were not included. Emissions that occur from manure application were included in the processes where this occurs (e.g., the crop cultivation processes) [19]. Waste management was included in the form of compost. In the frame of this research, the transport distance from the farm to the field did not exceed 10 km. A mass allocation principle approach (allocation based on significant characteristics of co-products; food oil, cake, and straw yield) was employed in this study. The results of this research may be used to motivate environmentally friendly farming systems and as a source of information on agricultural subjects that relate to farming practices (Bernas et al., 2021). The data were analyzed and evaluated by LCA standards [20,21].

2.2. Data Source and Life Cycle Inventory (LCI)

This study was based on the standards of agricultural practices related to the conditions of the Czech Republic [22] as the primary data source. Information on seed yield and straw yield were updated according to the Situation and Outlook Report on oil crops prepared by the Ministry of Agriculture of the Czech Republic [2,22]. Individual monocrops of selected oil crops were evaluated. Secondary data for background processes were taken from the Ecoinvent v3.7 [23], Agri-footprint v4.0 [24], and WFLDB [25] databases.

2.3. Software Data Inventorization

The cultivation approaches and fertilization intensity were set up according to standard intensive agricultural practices [22]. Data were related to the average conditions of the Czech Republic. Based on seed yield information [2,22], food oil yield level and cake yield level were determined. These data were used to determine the area needed for generating the same food oil yield. Information (input data) related to individual oil crops, the number and frequency of agrotechnical inputs, inputs from the technosphere, inputs from nature, information about emissions to water and air are included in the following table (Table 1). The mass allocation principle was set up according to outputs from the growing cycles of individual oil crops.

2.4. Determination of Field Emissions

The usage of mineral nitrogenous fertilizers results in the release of so-called direct and indirect emissions of N2O, NH3, NO3−, and NOx (expressed as dinitrogen monoxide and ammonia in Table 1). The following were taken into account in the monitoring of field and agricultural emissions: NH3 and NOx volatilization, NO3− leaching to groundwater, and nitrogen loss from leaching and surface outflow [26]. The risk of erosion was not considered in this study. The production of pesticides and herbicides, their active substances, and their distribution has been taken into account using data from the Ecoinvent 3.7 database [23], but the fate of the pesticides in the environment was not taken into account. Therefore, the toxicity impact cannot be considered as fully reflected.

2.5. Impact Assessment

A life cycle assessment method was used for environmental load quantification. The system boundaries were set from the cradle to the farm gate. The results of this research are related to the selected midpoint impact categories of climate change (kg CO2 eq), terrestrial acidification (kg SO2 eq), freshwater eutrophication (kg P eq), marine eutrophication (g N eq), terrestrial ecotoxicity (g 1,4-DB eq), freshwater ecotoxicity (g 1,4-DB eq), water depletion (m3 eq), human toxicity (kg 1,4-DB eq), and fossil depletion (kg oil eq). The Attributional approach was used for this study. Selected impact categories are suitable for agricultural LCAs [11,13]. SimaPro 9.2.0.1 software, ReCiPe Midpoint, Hierarchical (H) perspective V1.13/Europe Recipe H., an integrated method [27], and a cut-off system model approach were used for the assessment of the environmental aspects. One cubic metre of food oil and an area unit (land demand for generating the same volume of food oil) were used as functional units. The characterization approach was primarily used for data expression.

2.6. Study Limitations and the Study Completeness Check

Life cycle modelling of agricultural crops and subsequent evaluation of environmental impacts by the LCA method is a complex task. As the authors of the study, we are aware that there are always a number of issues that make objective and accurate evaluation difficult. (1) The study did not include the fate of pesticides and their metabolites in the environment, so the categories of ecotoxicity should not be considered complete. (2) The effect of the pre-crop, the balance of nutrients from the point of view of inputs from atmospheric deposition, mineralization, or decomposition, was not taken into account. (3) The case study was based on a dataset of standard cultivation procedures corresponding to the conditions of the Czech Republic. The results of the study, therefore, should not be considered as flat-rate. (4) The study compares the environmental impact associated with the volume of food oil production from rape, sunflower, and hemp, and the qualitative aspects of these oils were not taken into account.

3. Results and Data Interpretation

Based on the inventoried data and modelled standardized cultivation practices corresponding to the conditions of the Czech Republic, the results of environmental impact levels for winter rapeseed, sunflower, and hemp were determined, which correspond to nine impact categories. Characterization (Section 3.1 and Section 3.2) and normalization (Section 3.3) approaches were used for data interpretation purposes.

3.1. Interpretation Based on the Unit of Production

Contribution analysis was performed for oil crop monocultures according to the characterization model (Figure 1). The results are related to nine impact categories and transferred to the environmental impact level in percentages. According to the data interpretation, it was also possible to define different environmental impacts between individual oil crops. The functional unit for this expression was one cubic metre of food oil.
According to the trend of interpreted data corresponding to the characterization model (Figure 1), the most significant environmental impact related to 1 m3 of food oil was connected with rapeseed food oil production in the impact category of climate change, human toxicity, terrestrial ecotoxicity, water depletion, and fossil depletion. Within the impact categories of terrestrial acidification, freshwater eutrophication, marine eutrophication, and freshwater ecotoxicity, the highest environmental impact related to 1 m3 of food oil was connected with hemp oil. The differences in environmental impact levels between individual oil crops and impact categories were important. According to models of life cycles, sunflower oil can be considered a product with the lowest environmental impact compared to hemp and rapeseed oil. According to results based on the FU of production, the environmental impact of 1 m3 of food oil production of sunflower seems to be more environmentally friendly in comparison to hemp oil or rapeseed oil.
From the point of view of a contribution analysis, the impact on the environment was mainly reflected in the input of agrotechnologies and fertilizer production and utilization, and related to field emissions production. It was predominantly reflected in all the assessed impact categories. The inputs of agrotechnology—agrotechnical operations performed during pre-sowing tillage, fertilization and incorporation of fertilizers into the soil, application of plant protection products, and harvesting—had a substantial effect on the total environmental impact. These inputs were reflected mainly in the impact category of human toxicity, freshwater ecotoxicity, and fossil depletion, i.e., the category mostly related to the consumption of fossil fuels. A large share of the total impact on the environment belongs to the inputs of mineral fertilizers or their production and use. This input most affects the category of fossil depletion, water depletion, or human toxicity. In all cases, it was modelled with inputs of organic fertilizers (slurry or manure) and with the related field emissions. Their input does not manifest itself significantly. Apart from marine eutrophication, climate change, and terrestrial acidification (representing more than a 60% share of the environmental impact of hemp oil production), this input was low due to the nature and volume. Field emissions impact level then depended on the inputs of fertilizers (mineral and organic). In this study, the environmental impact associated with emissions to air (nitrogen oxides, dinitrogen monoxide, and ammonia) and emissions to groundwater (nitrate and phosphorus) from fertilizers were modelled. These emissions form a significant part of the environmental impact in the impact category of climate change (up to 55% in the case of winter rapeseed oil) and freshwater eutrophication (up to 60% in the case of hemp oil). Another input of growing cycles, with a relatively small impact (up to 6% on a total environmental load of impact categories), was land use. Land use was mainly reflected in the impact category of climate change and terrestrial ecotoxicity. The relatively high environmental impact was associated with the production and use of seeds (up to 50% in the case of hemp oil production, in terms of terrestrial ecotoxicity or marine eutrophication). The most affected impact category due to seed input and seed production was terrestrial ecotoxicity, and in comparison with the monitored oil crops, seed input was most pronounced for hemp. This affects the nature of the entry itself and the amount of seed needed to establish the stand (winter rapeseed 4, sunflower 5, and hemp 60 kg ha−1 of seed). Due to the higher demand for hemp seeds for sowing, this input was also reflected in the impact category of marine eutrophication or freshwater ecotoxicity. The last input considered was the production and usage of chemical plant protection products (pesticides, herbicides, and growth regulators). In sum, these inputs did not exceed (within the individual impact categories) 10% of the total environmental impact, except in the case of sunflower oil production under the impact category of terrestrial ecotoxicity (about 25% of the total environmental impact) and human toxicity (about 15% of the total environmental impact). However, it should be noted that their following distribution in the environment and the potential impacts of their residues were not taken into account.
Results were highly dependent on the inputs of the cultivation strategy (inputs and outputs) and on the final yield of seeds and the gain of food oil. Another critical aspect was the allocation approach (mass allocation principle), which determines the final share of the environmental impact.

3.2. Interpretation Based on Unit of Land Demand

The results of the environmental impact assessment from the point of view of the functional unit of area (the area of land needed for the generation of the same volume of food oil) differ widely from the assessment associated with the functional unit of production. The functional unit of equivalent area (land demand for generating the same volume of food oil) brought a significant change in the trend of environmental impacts. In the case of hemp, 6.8 ha were needed for the same volume of food oil which can be produced with 1.0 ha of land for winter rapeseed and 1.3 ha for sunflowers. From this perspective, hemp oil production was connected with the highest environmental impact in comparison to sunflower and rapeseed food oil production (Figure 2) within all assessed impact categories. The environmental impact level of hemp was affected by the high land demand and the related more substantial inputs to the life cycle and cultivation strategy.
Compared to the evaluation related to the functional unit of production, significant changes were found in hemp. The influence of field emissions and fertilizer inputs (mineral and organic) are most pronounced, though all inputs related to the growing cycle are represented. This was a proportional increase in the environmental impact, reflecting the higher demand for land to produce the same amount of food oil as rape and sunflower. The total environmental impact would increase two to nine times compared to sunflower or winter rapeseed, which showed a completely different trend. Thus, it turned out that assessing environmental impacts from the point of view of a unit of area is essential for a fair comparative study.

3.3. Normalization and the Data Weighing

Normalization of data sets was applied to take into account the most affected impact categories. No contribution analysis was employed for normalizations because percentage terms for individual impact categories would give identical characteristics to the characterization model. However, normalization is important for detecting the most affected categories, and therefore the components of the environment. Data normalization was done for both specified functional units (Figure 3 and Figure 4).
Following the normalization model (Figure 3), most affected were the categories of eutrophication and ecotoxicity. Fertilizer treatment, related field emissions, and agrotechnology creation were the most significant sources of environmental impact. In the impact category of fossil depletion, terrestrial ecotoxicity, human toxicity, and climate change, rapeseed oil production was related to the highest environmental impact. In the impact category of freshwater ecotoxicity, marine eutrophication, freshwater eutrophication, and terrestrial acidification, hemp oil was characterized by the highest environmental impact. The trend of environmental impact level points to the lower impact related to sunflower oil production (FU = 1 m3 of food oil).
A comparison of selected oil crops based on the normalization model was also made within the land demand for generating the same volume of food oil (Figure 4). According to the results, the impact categories with the highest environmental impact were the categories of eutrophication and ecotoxicity, which was similar to FU production (m3 of food oil). However, due to the higher demand for land in the case of hemp, the highest environmental impact was associated with the production of hemp oil in all assessed impact categories. The most striking increase was found in the category of freshwater ecotoxicity, freshwater eutrophication, terrestrial acidification, and human toxicity.
Although weighing provides only a general view of the overall environmental impact assessment, it is a suitable tool for data trend interpretation. A combination of both specified functional units within the weighing is suitable for data interpretation. Such a data expression can provide a comprehensive view of the assessed issues and thus determine the cultivation strategy, in this case, the oil crop with the lowest overall impact on the environment, and vice versa. This overall comparison is part of Figure 5.
According to the established study framework and models presenting winter rapeseed, sunflower, and hemp cultivation technologies, the environmental impacts were quantified according to the functional unit of production (1 m3 of food oil) and the unit of land (land demand for generating the same volume of food oil) within nine impact categories corresponding to agricultural LCA. Thus, two perspectives with different trends of environmental impacts were obtained. Within the evaluation of FU production (m3 of food oil), the highest impacts on the environment were associated with the production of hemp oil (Figure 5). Within the evaluation of the FU area (land demand for generating the same volume of food oil), the highest impacts on the environment were also associated with the production of hemp oil. The principle of data weighing, combining both functional units (Figure 5), was used to summarise the obtained data. Thus, a general trend for individual oil crops was obtained. From this point of view, sunflower oil production appeared to be the variant with the lowest overall impact on the environment, which was about 60% lower compared to the production of hemp oil, and about 20% lower compared to the production of rapeseed oil.
Within agricultural LCAs, the scope for detailed and deep discussion is often limited to methodological issues, as studies differ in their frameworks, data quality, and character, as well as their interpretations. Presenting the results as trends is thus a logical step, one that gives the discussion greater generality and makes it more readily understandable for readers.

4. Discussion and Perspective

A life cycle assessment method was chosen to model the life cycle of winter oil crops (rapeseed, sunflower, and hemp as an alternative). Due to its complexity, LCA is a very popular environmental management tool [13]. The results were related to impact categories corresponding to the requirements for the agricultural LCAs [11]. The approach to the elaboration of this study, the approach to modelling, the allocation approach, the functional unit (volume of food oil), the software used, and the source databases were similar to, for example, the study of Fridrihsone et al. [28,29], which also focused on oil crops.
Agriculture is widely perceived as a multifunctional production process. In addition to food, animal feed, and energy sources, non-commodity outputs, such as landscape management and ecosystem services, are also generated. However, LCA studies often focus only on the ecological/environmental sustainability of agricultural products, expressed in terms of impacts per unit of production, without any allocation between commodity and non-commodity outputs. This narrow view, which focuses only on production efficiency, can often favour conventional agricultural products, although when evaluated by other methods, these systems prove to be less environmentally friendly and less sustainable [30,31,32]. The solution to the issue of multifunctionality lies in choosing another functional unit that allows multifunctional outputs or allocating environmental impacts to the whole complex of products and services provided within the agricultural system [33]. The choice of the functional unit determines the nature of the study outputs and their interpretation and is one of the key moments in implementing the LCA study [34]. If the product has more functions, it is always necessary to select those relevant for the assessed system [35]. The functional unit provides the basis on which the input and output data are related. It must be clearly definable and measurable [21]. The functional unit thus expresses the measurable size of the function that we expect from the product system [35]. The universal solution seems to be to use both methods of calculating the environmental impact, both per unit area and per production unit [19,36]. Recent criticism points to the fact that these two functional units do not affect product quality, which can play a key role in defining product function. An example can be the types of quality wine [10]. In the LCA study of an agricultural commodity, more functional units should ideally be chosen for the examined system, contributing to a complete evaluation from several perspectives [37]. In addition, this step would clearly improve the comparability of the results with other studies of the same product [10].
The environmental aspects of rapeseed cultivation, from the LCA perspective, have recently received a relatively large amount of attention (e.g., [8,9,28,29]). This is because rapeseed oil was long thought to cause a lower environmental impact compared to mineral oils, for example. However, it has been shown that the systems running on rapeseed oil are not necessarily better for the environment. Many of the environmental issues examined in one study were affected more negatively by the use of rapeseed oil than mineral oil. The main exception to this was greenhouse gas emissions, which are consistently higher for systems using mineral oil because of the use of fossil resources for rapeseed oil production [38]. As Stow et al. [39] stated, biodiesel based on rapeseed is often considered to improve energy security and reduce the impact of fuel on climate change. However, there are concerns about the impact of biodiesel when its life cycle is considered. The potential impact of using biodiesel rather than conventional diesel was investigated using a life cycle assessment (LCA) of rapeseed biodiesel. Biodiesel leads to reduced fossil fuel use and is likely to reduce the impact of transport on climate change. However, it was found that the impact of biodiesel towards other categories, i.e., land use and respiratory inorganics (Particulate matter; PM2.5), was greater than petroleum diesel. Therefore, biodiesel production should be carefully managed to mitigate its impact on the environment.
Our study shows how the cultivation practices and the type/quantity of input influence the total environmental impact. Using the Life Cycle Assessment (LCA) method to assess the environmental impact of rapeseed and sunflower was also performed in the study of Palmieri et al. [8]. The study presents similar findings to ours. The practice of intensive farming with high fertilization and mechanization (machinery and fertilizer production and application) is responsible for the high environmental impact. However, when the level of productivity is low, the impact is still higher [8]. The results of our study also show that the highest environmental impacts would be associated with the production of hemp oil in comparison with rapeseed oil and sunflower oil. The results of Iriate et al. [40] also indicated that, compared to sunflower, rapeseed production has a better environmental performance (in nine out of the eleven impact categories evaluated) and lower water consumption. Although this study did not use the same methodological approach and framework to the present study, the trend of environmental aspects is similar. Iriate et al. [40] added that the energy demand of rapeseed is 4.9 GJ t−1 seed, 30% less than that of sunflower. Mineral fertilizers cause the highest environmental impact. According to Queiros et al. [41], the choice of fertilizer has strong implications for environmental impacts. The production of nitrogen fertilizers makes significant contributions to abiotic depletion, global warming, ozone layer depletion, and photochemical oxidation. The analysis of the life cycle of fertilizers indicates that extraction of raw materials and their production are key stages. Attempts to reduce the environmental impact and energy requirement of both crops should be mainly associated with the evaluation of other types of fertilization. In addition, particularly for sunflowers, low-impact herbicides should be evaluated, seed yield improved, and cultivation practices optimized [40].
Based on the study results and the assessed framework, a number of inputs contribute to the total environmental impact, and one of the most important is agrotechnical operations in general. The impact of agricultural technology was significantly reflected in the category of freshwater ecotoxicity (about 50–70% of the total impact when the FU of production was considered), where the main role was played by fuel and energy consumption. Other significantly affected categories are fossil depletion (about 33–42%) and human toxicity (about 25–33%). From a general point of view, agrotechnical operations can be divided into those that need fuel for their operation (chief amongst which is diesel-based agriculture) and those that need electricity or natural gas. The need for natural gas (e.g., for heating greenhouses) did not occur in the evaluated study. Post-harvest processing of agricultural raw materials (in our case, food oil processing was not reflected in the study framework) and irrigation systems both depend on electricity (though not in the case of this study). With respect to common field operations and fuel consumption, ploughing was a major factor (and thus a place to improve the product’s environmental profile). Based on the study result, ploughing also had one of the dominant roles among agrotechnical inputs. One possibility for optimization is to shift to reduced or even no-tillage systems. Fuel consumption and energy input are much lower than in the conventional tillage system using a plough, but yields do not differ, as shown for maize, soybean, sugar beet, and winter wheat [42,43,44]. Minimization technologies or no-till systems are an alternative to energy-intensive operations. They use shallower tillage [45,46], e.g., by loosening or sowing surface-treated or untreated soil [47]. However, the impact on the final yield level has to be considered [46].
One of the most important inputs in the agricultural phase is that of fertilizers (organic and inorganic) [48,49]. For the reduction of greenhouse gas emissions from agricultural crop production, it is proposed to reduce the doses of nitrogen fertilizers used [50]. Reducing doses, especially of synthetic nitrogen, brings significant economic savings, in addition to the environmental benefits, which could provide an incentive for farmers to manage nitrogen properly, including the use of closed-cycle N-cycle recycling techniques [51]. It is also necessary to follow the principles of proper management of nitrogen fertilizers [52]. Furthemore, the nitrogen that is accessible through biological fixation is potentially high, as shown for faba beans and peas [53], not just in organic systems but also in conventional farming where nitrogen fertilizer is used [54,55]. The reduction of synthetic fertilizers can also be achieved through organic farming [56] or agroecological techniques [57]. Both of these concepts have a long tradition in the Czech Republic [58]. However, organic production is often associated with lower production per unit area, and with it often higher environmental pressures [59]. One way to support the reduction of the environmental impact of organic farming is to increase its yields while maintaining existing inputs [60]. This can be achieved, for example, by using a more balanced sowing procedure or by more efficient application and use of fertilizers [48]. The significant contribution of nitrogen fertilizers to the environmental impacts of rapeseed cultivation emphasizes the need for efficient nutrient management practices in order to minimize the application rates required [41]. Precise agricultural practices can be used for the purposes of minimizing fertilizer doses. For example, Nedbal et al. [61] showed how the most modern methods of spectral evaluation of plant nutrition can be used to calculate precise doses of nitrogen fertilizer. These techniques can help to decrease the leaching of nitrates into ground and surface water.
Transport is usually an important part of the life cycle assessment of agriculture and food production. Its importance and impact are growing mainly due to globalization tendencies [62]. It is often expressed in terms of “food miles”, which summarize all the logistical routes of a product between farmers, producers, and consumers [63]. In the evaluated cycles, the transport was created using a tonne-kilometre (tkm), which expresses the transport of one ton of cargo over a distance of one kilometre. All modelled transport was realized with the help of road freight transport, and the transport distance was considered in the study to be 10 km. Only transport between the field and the farm was taken into account in the study. Overall, transport can be considered a minority input, as its share within the individual impact categories did not exceed 5%.
Based on the study results, the input of plant protection products did not exceed a 10% share of the total impact. However, it should be noted that the fate of pesticides in the environment was not considered, but only their impact arising from the production and application as represented in the databases (Ecoinvent v3.7 [23], Agri-footprint v4.0 [24], and WFLDB [25]). Within agricultural LCAs, field emissions of pesticides are quantified by modelling [64]. Despite the fact that from the point of view of the established framework and the nature of the inputs, sunflower and rape appear to be more environmentally friendly options compared to hemp, it is necessary to take into account aspects related to the use of pesticides. The fate of pesticides in the environment and their impact can be crucial when deciding on the application of plant cultivation strategies or their removal from the environment [65]. Based on the study related to the Czech Republic, the side effects of pesticides are one of the major factors often linked to bee colony losses. The most important pesticides related to the poisoning incidents were highly toxic chlorpyrifos, deltamethrin, cypermethrin, imidacloprid, and slightly toxic prochloraz and thiacloprid. Importantly, poisoning was associated with pesticide cocktail applications. Almost all poisoning incidents were investigated in relation to rapeseed [66]. Sunflower cultivation is also highly dependent on pesticides [67]. It is common practice in the Czech Republic to apply fungicides and pesticides together. This step also has an impact on biodiversity, including bee populations [68]. In contrast, hemp is grown without agrochemical inputs without any problems [17], thus eliminating the negative factors associated with them. It is still important to monitor the fate of pollutants and foreign substances in the environment. Due to the importance of the topic, this is an issue requiring appropriate attention. There are still many questions about the transport and behaviour of pollutants, their interactions with other substances, and the impact on human health. Effective ways for reducing their usage and achieving suitable management must be found [69].
Compared to sunflowers and rapeseed, hemp production has several other significant environmental benefits [70]. One of these is high sequestration. The soil carbon change associated with different agricultural management practices is an important factor contributing to the global warming impact [41]. In the case of hemp production, sequestration is up to 2500 kg CO2 per ha per year [71]. In the case of rapeseed, carbon sequestration to soils varies between 112 kg CO2 eq/1000 kg dry seeds (cool temperate dry climate) and 271 kg CO2 eq/1000 kg dry seeds (warm temperate moist climate) [41]. According to Halvorson et al. [72], with no-till, an estimated 854 kg CO2 ha−1 was sequestered each year in the annual crop system, which included sunflowers, compared with 92 kg CO2 ha−1 with minimum till and a loss of 517 kg CO2 ha−1 with conventional till. With respect to carbon sequestration, soils with high organic carbon content should not be converted to rapeseed cultivation to avoid excessive carbon emissions [41]. Another benefit of hemp that was not taken into account in the study is soil erosion. Whereas sunflowers belong to the category of plants with high erosion risk, and rapeseed belongs to the category of plants with mean erosion risk [73], hemp can enrich and stabilize unproductive lands by reducing weed pressure and soil erosion [70].
The demand for hemp products is growing. Hemp is considered an environmentally friendly crop with a lower environmental impact and higher yields, and can replace traditional materials used in the building, car, textile, paper, and biofuel industries. In addition to these benefits, hemp is also used in the food industry, as hemp seeds are rich in fat and proteins. Furthermore, demand for dietary supplements will grow as more consumers are looking for healthy or vegan food alternatives [5]. Hemp is an excellent plant for cultivation in organic farming systems [74] and is suitable for crop rotation [75].

5. Conclusions

The study presents the results of environmental impact assessments from the perspective of an agricultural LCA. The results concern the environmental issues associated with the production of vegetable food oil. According to the established study framework and data corresponding to standard cultivation practices for winter rape, sunflower, and hemp, hemp cultivation for food oil production may not meet the high sustainability predictions and low environmental impacts that are currently claimed for it. In this respect, the inputs to the growing cycle, and especially the low yields of food oil compared to traditional and efficient oils crops, including winter rape and sunflower, are significant. The applied methodological approach and interpretation of data in this study showed that the total environmental impact (based on the combination of production and area unit) associated with the production of hemp oil (volume of food oil) was about 40% higher than rapeseed oil and about 60% higher than sunflower oil.

Author Contributions

Conceptualization, J.B., T.B., V.N., and R.W.N.; methodology, J.B.; software, J.B.; validation, J.B., T.B., V.N., and R.W.N.; formal analysis, J.B., T.B., V.N., and R.W.N.; investigation, J.B.; resources, J.B.; data curation, J.B., T.B., V.N., and R.W.N.; writing—original draft preparation, J.B., T.B., V.N., and R.W.N.; visualization, J.B., T.B., V.N., and R.W.N.; supervision, R.W.N.; funding acquisition, T.B. All authors have read and agreed to the published version of the manuscript.

Funding

The research was financially supported by the Grant Agency of the University of South Bohemia in České Budějovice, Czech Republic under grant number GA JU 045/2019/Z, and by the Faculty of Agriculture, the University of South Bohemia in České Budějovice.

Institutional Review Board Statement

Not applicable.

Informed Consent Statement

Not applicable.

Data Availability Statement

All the data related to this manuscript are available in this document or they were cited in the references.

Acknowledgments

The authors would like to thank the Faculty of Agriculture, the University of South Bohemia in České Budějovice, for their financial and material support. We would like to thank our colleagues for their help with administrative support and manuscript preparation. We finally want to warmly thank the anonymous reviewers for their comments, which improved the quality of the paper.

Conflicts of Interest

The authors declare no conflict of interest.

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Agronomy 11 02301 g001 550
Figure 1. Environmental impact level for the unit of production (FU = 1 m3 of food oil). Contribution analysis from the cradle-to-farm gate approach for environmental impacts; ReCiPe midpoint (H) method, characterization model, results were expressed per 1 m3 of food oil.
Figure 1. Environmental impact level for the unit of production (FU = 1 m3 of food oil). Contribution analysis from the cradle-to-farm gate approach for environmental impacts; ReCiPe midpoint (H) method, characterization model, results were expressed per 1 m3 of food oil.
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Figure 2. Environmental impact level for the unit of area (FU = land demand for generating the same volume of food oil). Contribution analysis from the cradle-to-farm gate approach for environmental impacts; ReCiPe midpoint (H) method, characterization model, results were expressed per land demand for generating the same volume of food oil.
Figure 2. Environmental impact level for the unit of area (FU = land demand for generating the same volume of food oil). Contribution analysis from the cradle-to-farm gate approach for environmental impacts; ReCiPe midpoint (H) method, characterization model, results were expressed per land demand for generating the same volume of food oil.
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Figure 3. Normalization model for the unit of production (FU = 1 m3 of food oil). From the cradle-to-farm gate approach for environmental impacts; ReCiPe midpoint (H) method, normalization model, results were expressed per 1 m3 of food oil.
Figure 3. Normalization model for the unit of production (FU = 1 m3 of food oil). From the cradle-to-farm gate approach for environmental impacts; ReCiPe midpoint (H) method, normalization model, results were expressed per 1 m3 of food oil.
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Figure 4. Normalization model for the unit of area (FU = land demand for generating the same volume of food oil). From the cradle-to-farm gate approach for environmental impacts; ReCiPe midpoint (H) method, normalization model, results were expressed per land demand for generating the same volume of food oil.
Figure 4. Normalization model for the unit of area (FU = land demand for generating the same volume of food oil). From the cradle-to-farm gate approach for environmental impacts; ReCiPe midpoint (H) method, normalization model, results were expressed per land demand for generating the same volume of food oil.
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Figure 5. Weighing based on normalization mode. Production unit = 1 m3 of food oil; Area unit = land demand for generating the same volume of food oil; Combination = interpretation based on the merger of both functional units.
Figure 5. Weighing based on normalization mode. Production unit = 1 m3 of food oil; Area unit = land demand for generating the same volume of food oil; Combination = interpretation based on the merger of both functional units.
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Table
Table 1. Inventory table: inputs and outputs of the life cycle.
Table 1. Inventory table: inputs and outputs of the life cycle.
UnitRapeseedSunflowerHemp
Outputs
Seeds yieldkg ha−135002800500
Straw yieldkg ha−1420070009000
Cake yieldkg ha−12206.41715.8409.9
Food oilL ha−11293.61084.2190.2
Seed oiliness%424436
Cake oiliness%121212
Land demand for generating the same yield #ha11.36.8
Mass allocation principle (based on outputs)
Food oil%EL16.811.061.98
Cake%EL28.6517.514.27
Straw%EL54.5571.7593.75
Inputs from technosphere—Material/fuels
Tillage, cultivating, chisellingha0.80.22
Tillage, rollingha0.3–2
Tillage, harrowing, by spring tine harrowha0.31.6–
Tillage, harrowing, by offset levelling disc harrowha–0.3–
Tillage, harrowing, by offset disk harrowha–1–
Fertilizing, by broadcasterha1.451.10.87
Potassium chloride, as K2O, at plantkg ha−11599
Phosphoric acid, as P2O5, at plantkg ha−123.03––
Ammonium nitrate phosphate (ANP), as P2O5, at plantkg ha−1–9–
Triple superphosphate, as P2O5, at plantkg ha−1––19.75
Solid manure loading and spreadingkg ha−112,00010,0004000
Manure, solid, cattlekg ha−112,00010,0004000
Tillage, ploughingkg ha−1110.1
Application of plant protection product by field sprayerkg ha−15.94.91.4
Napropamideg ha−190––
Herbicide, unspecified, mix for oil crops, at plantkg ha−12.293.652.45
Fungicide, unspecified, mix for oil crops, at plantkg ha−1–6.1–
Sowingha111
Seedskg ha−14560
Chloroacetanilide herbicides, at plantg ha−1372––
Metaldehydeg ha−140––
Fluazifop-p-butyl, at plantg ha−175––
Calcium ammonium nitrate (CAN), as N, at plantkg ha−1266.3–40
Nitrogen fertiliser, as Ng ha−1126––
Manure management, cattle, liquid-slurry, warm, per kg DMkg100–200
Slurry application, spreader with trailed hoses, per m3m3 ha−12–4
Dinitrophenol herbicides, at plantg ha−10.12––
Ammonium nitrate (AN), as N, at plantkg6070–
Plant growth regulator, at plantg0.370.2–
Urea ammonium nitrate (UAN) (with 30% N), at plantkg ha−10.090–
Magnesium oxidekg ha−10.033.5–
Sulfurkg ha−10.024––
Boric oxidekg ha−10.018––
Insecticide, unspecified, mix for oil seed crops, at plantkg ha−10.650.250.25
Combine harvestingha111
Transport, tractor, and trailer, agriculturaltkm35285
Land-use change, annual crop, annualized on 20 yearsha111
Inputs from nature
Land occupation *ha111
Water (as a medium for plant protection products) *L ha−120401470557.5
Emissions to air
Nitrogen oxides, CZkg ha−11.751.210.31
Dinitrogen monoxidekg ha−18.325.741.46
Ammonia, CZkg ha−111.866.0110.29
Emissions to groundwater
Nitratekg ha−10.2760.2650.169
Phosphoruskg ha−10.8480.2660.275
# Basis is the treatment with the highest food oil yield (1 ha of winter rapeseed). * Input/s from the Ecoinvent, Agri-footprint, or WFLDB database. Transport was included in the process with a flat rate 10 km × yield achieved (max 8 tons per load). tkm = tonne-kilometre; %EL = share on the total environmental impact level; DM = dry matter.
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Bernas, J.; Bernasová, T.; Nedbal, V.; Neugschwandtner, R.W. Agricultural LCA for Food Oil of Winter Rapeseed, Sunflower, and Hemp, Based on Czech Standard Cultivation Practices. Agronomy 2021, 11, 2301. https://0-doi-org.brum.beds.ac.uk/10.3390/agronomy11112301

AMA Style

Bernas J, Bernasová T, Nedbal V, Neugschwandtner RW. Agricultural LCA for Food Oil of Winter Rapeseed, Sunflower, and Hemp, Based on Czech Standard Cultivation Practices. Agronomy. 2021; 11(11):2301. https://0-doi-org.brum.beds.ac.uk/10.3390/agronomy11112301

Chicago/Turabian Style

Bernas, Jaroslav, Tereza Bernasová, Václav Nedbal, and Reinhard W. Neugschwandtner. 2021. "Agricultural LCA for Food Oil of Winter Rapeseed, Sunflower, and Hemp, Based on Czech Standard Cultivation Practices" Agronomy 11, no. 11: 2301. https://0-doi-org.brum.beds.ac.uk/10.3390/agronomy11112301

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