Figures
Abstract
Greenhouse gas emissions associated with pesticide applications against invasive species constitute an environmental cost of species invasions that has remained largely unrecognized. Here we calculate greenhouse gas emissions associated with the invasion of an agricultural pest from Asia to North America. The soybean aphid, Aphis glycines, was first discovered in North America in 2000, and has led to a substantial increase in insecticide use in soybeans. We estimate that the manufacture, transport, and application of insecticides against soybean aphid results in approximately 10.6 kg of carbon dioxide (CO2) equivalent greenhouse gasses being emitted per hectare of soybeans treated. Given the acreage sprayed, this has led to annual emissions of between 6 and 40 million kg of CO2 equivalent greenhouse gasses in the United States since the invasion of soybean aphid, depending on pest population size. Emissions would be higher were it not for the development of a threshold aphid density below which farmers are advised not to spray. Without a threshold, farmers tend to spray preemptively and the threshold allows farmers to take advantage of naturally occurring biological control of the soybean aphid, which can be substantial. We find that adoption of the soybean aphid economic threshold can lead to emission reductions of approximately 300 million kg of CO2 equivalent greenhouse gases per year in the United States. Previous studies have documented that biological control agents such as lady beetles are capable of suppressing aphid densities below this threshold in over half of the soybean acreage in the U.S. Given the acreages involved this suggests that biological control results in annual emission reductions of over 200 million kg of CO2 equivalents. These analyses show how interactions between invasive species and organisms that suppress them can interact to affect greenhouse gas emissions.
Citation: Heimpel GE, Yang Y, Hill JD, Ragsdale DW (2013) Environmental Consequences of Invasive Species: Greenhouse Gas Emissions of Insecticide Use and the Role of Biological Control in Reducing Emissions. PLoS ONE 8(8): e72293. https://doi.org/10.1371/journal.pone.0072293
Editor: Subba Reddy Palli, U. Kentucky, United States of America
Received: April 23, 2013; Accepted: July 14, 2013; Published: August 20, 2013
Copyright: © 2013 Heimpel et al. This is an open-access article distributed under the terms of the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original author and source are credited.
Funding: 1. The University of Minnesota Institute on the Environment. They provided a fellowship for the corresponding author of $50,000. This will be used to cover publication charges; http://environment.umn.edu/research/residentfellows2011.html . 2. The University of Minnesota Agricultural Experiment station provides $6,000 per year to the laboratory of the corresponding author so long as the work is focused on biological control i Minnesota. This fund was used for photocopying associated with the project; http://www.maes.umn.edu/. The funders had no role in study design, data collection and analysis, decision to publish, or preparation of the manuscript.
Competing interests: The authors declare that no competing interests exist.
Introduction
Many pest organisms reach their most damaging levels away from their native geographic range. This general pattern has been documented for weeds [1], insect pests [2], and pathogens [3,4] among others. Extensive bodies of literature have developed around both the causes and consequences of invasive pests [5–7]. Although invasive species can cause considerable economic and ecological damage [8–10], biotic resistance by competitors and consumers of introduced species can greatly attenuate this damage (e.g. [11–13]). Here, we consider the implications of an invasive agricultural pest for greenhouse gas emissions associated with controlling the pest. Our goal is to estimate the actual emission costs incurred by the invasion as well as the hypothetical emissions that would occur in the absence of biotic resistance in the form of naturally occurring biological control. This allows an estimation of the role of biological control in attenuating greenhouse gas emissions of an invasive pest.
Numerous recent analyses link global climate change to invasive species (e.g. [14–16]). Most of these analyses focus on effects of climate change on the spread or consequences of invasive species, but the converse of this relationship - effects of invasive species on climate change – remains virtually unexplored. The only such analysis of which we are aware is the one by Kurz et al. [17], which showed how climate change-induced spread of bark beetles in Canada can lead to reduced carbon sequestration. Our analysis highlights another effect of invasive species on climate change: impacts of invasive species on greenhouse gas emissions. By virtue of their increased abundance in introduced ranges, invasive pests require disproportionately high levels of management intervention, including efforts at eradication and control [8]. We focus on greenhouse gas emissions associated with insecticide use to control the soybean aphid, Aphis glycines, a recent invasive agricultural pest in North America.
The soybean aphid is native to eastern Asia and was first detected in North America in the summer of 2000. Although insect predators are important in reducing the damaging effects of the soybean aphid, this insect has emerged as the most important pest of soybeans in North America [18]. Management of the soybean aphid has been primarily through application of insecticides although alternative management tactics including host-plant resistance and the importation of Asian biological control agents are also under development [18–20].
Our aim in this paper is to calculate the life cycle greenhouse gas emissions associated with insecticide use against the soybean aphid in the United States, taking into account insecticide manufacture, transport, and application. Other researchers have prepared energy budgets and have estimated greenhouse emissions for various agricultural practices including pesticide use [21–25], but to our knowledge this is the first analysis focused on a particular pest species. We also consider the extent to which economic spray thresholds [26,27] and naturally occurring biological control (e.g. [28–31]) can mitigate carbon emissions associated with soybean aphid control.
Analysis and Results
Our estimate of life cycle greenhouse gas emissions induced by chemical control of soybean is divided into emissions associated with insecticide manufacture, transport, and application. We use estimates of insecticide application associated with soybean aphid control from the United States Department of Agriculture National Agricultural Statistics Service (USDA NASS) Agricultural Chemical Usage Field Crops Summary databases. These databases provide state-level data on quantities applied (L ha-1) and acreage (ha) treated and are available for insecticide use in soybeans from 1991 through 2002 and from 2004 through 2006. We focus exclusively on the 12 states within the North-central region of the U.S., as defined by USDA NASS – Illinois, Indiana, Iowa, Kansas, Michigan, Minnesota, Missouri, Nebraska, North Dakota, Ohio, South Dakota and Wisconsin. The rationale for not including data from other states is that farmers in some other states, particular in the southeastern U.S., apply insecticides against insect pests other than the soybean aphid [32–34]. Soybean acreage in the North-Central states, on the other hand, received almost no insecticide application prior to the arrival of soybean aphid. It is therefore likely that most if not all of the application of insecticides in these states following the arrival of soybean aphid was directed at soybean aphid [18,26]. The 12 states used in our analysis cover approximately 80% of the approximately 38 million hectares of soybeans planted each year in the U.S.
Manufacture
We used information on the amount of active ingredient (A.I.) of insecticide applied per year against soybean aphid to estimate emissions associated with insecticide manufacture and transport. The amounts of insecticide applied were too low to be reported by USDA NASS between 1991 and 1998 although some acreage was reported treated in 1991 and 1992 (Figure 1). In 1999 – the year before soybean aphid was detected in North America -15,400 kg of insecticides were applied to soybeans in North-Central states against other insects. The figure was about one-third of this amount in 2000 but then increased to almost 0.9 million kg by 2006 (Figure 1).
Data are from the U.S. Department of Agriculture National Agricultural Service, from which data on insecticide use in soybeans were available for the years 1991-2002 and 2004-2006.
The main insecticides used against soybean aphid were chlorpyrifos (an organophosphate), lambda-cyhalothrin, and esfenvalerate (both pyrethroids) with lesser use of zeta-cypermethrin and permethrin (both pyrethroids as well). The relative percentages of chlorpyrifos, lambda-cyhalothrin, and esfenvalerate used over the entire reporting period were 38%, 47%, and 15%, respectively, according to the USDA NASS database. All three compounds are broad-spectrum insecticides that exhibit high toxicity to honeybees, other beneficial insects including biological control agents of aphids, and vertebrates (e.g. [35–37]). The neonicotinoid class of insecticides are used as a seed treatment targeting soybean aphid as well [38,39] but these compounds are not tracked by USDA NASS, so we do not consider them here.
Energy inputs associated with insecticide manufacture include the raw materials themselves, which are typically petroleum or natural gas, and the transformation of these materials into insecticides using a variety of energy-intensive industrial processes [25]. A life cycle analysis also includes energy inputs needed to build manufacturing plants and related operations, as well as those needed to extract the fuel needed for manufacture. Green [25] was the first to construct life cycle energy budgets for pesticide manufacture with these principles in mind and his analyses, although only approximations, have been used by a number of authors and remain the most reliable estimates to date [40–42]. Green [25] produced estimates for 39 commonly used pesticides, 11 of which are insecticides. These compounds did not include the three foliar insecticides used against soybean aphid noted above, but other organophosphates and pyrethroids were represented. Our approach here is to use the information provided by Green [25] for insecticides belonging to the same class of compounds in our analysis of the manufacture of soybean aphid insecticides. Specifically, we use Green’s energy values for cypermethrin to approximate values for lambda cyhalothrin and esfenvalerate since all three are classified as fourth-generation pyrethroids [43] or as Type II pyrethroids based upon their chemical structure [44]. To approximate energy use associated with chlorpyrifos, we use Green’s values for methyl parathion since both insecticides are classified in the same subclass of organophosphate insecticides, the phosphorothiolates [44].
The estimate of energy inputs provided by Green [25] reported proportions of different energy and material inputs used to manufacture various pesticides. Here we convert Green’s estimates associated with manufacturing and transport to their greenhouse gas emissions factors. Green’s analyses reported energy use in joules, from which we derive estimates of CO2 equivalent (CO2e) greenhouse gas emissions based upon global warming potential. The three main greenhouse gasses are CO2, methane (CH4), and nitrous oxide (N2O), which have default standardized 100-year global warming potentials of 1, 25, and 298, respectively [45]. Further, Green included both process energy (fuel oil, electricity, and steam) used or combusted on-site, and inherent energy (naphtha, natural gas, and coke) used as material feedstock and these processes require different conversion factors to CO2e. For process-energy related greenhouse gas emissions, we applied the following emission conversion factors: 0.090 kg CO2e MJ-1 for fuel oil, 0.095 kg CO2e MJ-1 for steam generated from fuel oil and 0.772 kg CO2e kWh-1 for electricity. These emission factors were taken from the Ecoinvent v. 2.2 database [http://www.ecoinvent.ch/] reflecting US emissions. For feedstock-associated GHG emissions, we applied the following emission factors: 0.005 kg CO2e MJ-1 for naphtha, 0.016 kg CO2e MJ-1 for natural gas and 0.018 kg CO2e MJ-1 for coke (Greenhouse Gases, Regulated Emissions and Energy Use in Transportation Model (GREET); http://greet.es.anl.gov/). Finally, to estimate the eventual acreage onto which insecticides were applied in the field based on the documented manufacture rates (Figure 1), we used the application rates from insecticide labels to estimate the amount of active ingredient of each insecticide used per hectare.
The values and calculations outlined above are presented in Table 1 for the three foliar insecticides commonly used against soybean aphid. Based on the relative use of these insecticides, and their application rates, our calculations lead to an estimate of 6.93 kg of CO2e greenhouse gasses emitted per hectare sprayed. These analyses illustrate the differences in emissions associated with the different insecticide classes. For instance, while the manufacture of pyrethroids (such as lambda cyhalothrin and esfenvalerate) is more energy intensive than manufacture of organophosphates (such as chlorpyifos), the much lower application rate of pyrethroids [46] offsets this difference so that the pyrethroids result in lower per-hectare emissions (Table 1).
| Soybean aphid insecticide (relative use) | Corresponding compound | Total energy inputs (MJ/kg)a | kg CO2e/ kg A.I.: Manufacture | kg CO2e/kg A.I.: Transportation | Application rate (kg [A.I.]/Ha) | Kg CO2e/Ha: Manufacture | kg CO2 e/ha: Transport | kg CO2e/Ha: Manufacture + Transport |
|---|---|---|---|---|---|---|---|---|
| Lambda cyhalothrin (0.47) | Cypermethrin | 580.000 | 65.165 | 0.082 | 0.022 | 1.434 | 0.002 | 1.436 |
| Esfenvalerate (0.15) | Cypermethrin | 580.000 | 65.165 | 0.082 | 0.045 | 2.934 | 0.004 | 2.938 |
| Chlorpyrifos (0.38) | Methyl Parathion | 160.000 | 18.198 | 0.082 | 0.841 | 15.306 | 0.069 | 15.376 |
| Totals weighted by relative use | 420.400 | 47.340 | 0.082 | 6.931 | 0.028 | 6.958 |
Table 1. Summary of life cycle analysis for greenhouse gas emissions associated with the manufacture and transportation of foliar insecticides against the soybean aphid in the United States.
Transportation
Energy inputs associated with the transportation of insecticides from the manufacturing plant to the farm includes three steps: (1) transport from the plant to a distribution center, (2) transport from the center to a mixing facility where ingredients are combined, and (3) transport from the mixing facility to the farm. An analysis by Wang [47] estimated 837 km for the one-way distance for step (1) based upon the typical regional distribution of insecticide manufacturing plants and we use this estimate for our analysis. Wang further assumed that this transport would typically be achieved by barge or rail transport, which have very similar GHG emissions (0.046 and 0.050 kg CO2e per ton*km, respectively; Ecoinvent v. 2.2). Steps (2,3) were estimated to be 80 and 48 km respectively, with corresponding GHG emissions of 0.134 and 0.239 kg CO2e per ton*km respectively, based upon the type of trucks typically used for these steps (Ecoinvent v. 2.2). Total emissions associated with these transportation steps converted to CO2 equivalents per hectare eventually sprayed are shown in Table 1. The overall value, weighted by the insecticides used is just under 0.03 kg CO2e ha-1, thus bringing the emissions associated with both manufacture and transportation to 6.96 kg CO2e ha-1 (Table 1).
Application
Greenhouse gas emissions associated with insecticide application are a function of the total acreage sprayed and the number of applications per year. In the 9 years prior to the arrival of soybean aphid, between 0 and 90,500 hectares of soybeans received insecticides in the North-Central U.S. (average between 1991 and 1999 = 24,700 hectares per year). Between 2000 and 2006, however, soybean acreage receiving insecticides increased to a maximum of 3.85 million hectares per year in 2006 (average between 2000 and 2006 excluding 2003, for which there is no data = 1.4 million hectares per year). The acreage sprayed in 2006 represented 19% of the total soybean acreage in the 12 North-Central states. According to USDA NASS, applications were made once per year in individual fields, with multiple applications rarely recorded. For simplicity, we therefore based our calculations on a single application per year.
Ground application was the dominant mode of insecticide application against soybean aphid [48] and many farmers in the region purchased specialized spray equipment for tractors in response to soybean aphid [26]. Furthermore, Helsel [23] noted that the energy used for ground and air application of pesticides is similar on large acreages. For simplicity we therefore base our calculations on ground application only.
To estimate emissions associated with ground application, we used values from the GREET database [24]. The GREET estimate of emissions due to application of any insecticide is 3.60 kg CO2e greenhouse gases per hectare, which is due to the use of diesel fuel, which is estimated at 1.2 liters per hectare for tractor-drawn sprayers [49]. The practice of ‘tank-mixing’ insecticides with herbicides, fertilizers and fungicides can lead to a lower level of applications dedicated to insecticide use. In one estimate, tank-mixing with the herbicide glyphosate accounted for nearly 40% of soybean aphid insecticide applications in 2007 [48], with much lower incidence of tank-mixing with fertilizer and undocumented levels of mixing with fungicide. However, these practices were not widely used during the time of our analyses [48] and they are not recommended because of reduced effectiveness of the insecticide [50].
In Figure 2, we show the estimated total CO2 equivalent greenhouse gases emitted per year due to manufacture, transportation and application of active ingredients of foliar insecticide against soybean aphid based upon acreage treated from Figure 1. We estimated that the use of foliar insecticides against the soybean aphid in the United States leads to approximately 10.6 kg of CO2 equivalent GHGs emitted per hectare sprayed -7.0 kg from insecticide manufacture and transport, and 3.6 kg from the application process.
Estimates are provided for the years since soybean aphid was first detected in the U.S. and estimates of insecticide usage were reported by the United States Department of Agriculture National Agricultural Statistics Service (USDA NASS).
Spray thresholds and biological control
A number of factors can mitigate insecticide use against soybean aphid, maintaining greenhouse gas emissions below what they otherwise would be. These include the development of a spray threshold for soybean aphid and the action of aphid consumers in suppressing soybean aphid below the threshold level. An economic spray threshold is the pest density at which a farmer must spray to avoid economic yield loss exceeding the cost of the application. In the absence of a threshold, farmers tend to spray on a schedule even when the pest is absent or at very low levels. For soybean aphid, a study done across the North-Central region of the U.S. calculated a threshold of 250 aphids per plant [26]. This threshold began to be disseminated in 2004 and was increasingly adopted throughout the region, replacing prophylactic treatment which leads to unnecessary application [27,48].
One of the main reasons that pest densities remain below threshold levels is that they are consumed by natural enemies. The role of naturally occurring predators and parasitoids in maintaining soybean aphid below the 250 per-plant threshold has been determined [30,51], and the extent to which these ‘biocontrol services’ lead to reductions in insecticide use has been calculated [52]. These analyses suggested that between 60 and 100% of soybean fields would exceed threshold levels in the absence of natural biological control and insecticide use, depending on aphid pressure in a particular year. In contrast, only 0-30% of fields actually exceeded threshold in the presence of aphid natural enemies, primarily lady beetles in these studies. This latter range of values encompasses the status quo and illustrates the value of the threshold over prophylactic treatments (i.e. preventative spraying in every field). Over the 30 million hectares of soybeans in the North-Central U.S., prophylactic spraying would result in emissions of 318 million kg CO2e greenhouse gases; full adoption of the threshold would reduce this by 70-100%.
Using a spray threshold allows for biological control to drastically reduce the need for insecticide applications. If we assume that 80% of the acreage would exceed threshold in the absence of aphid enemies in a typical year and 15% in the presence of enemies [52], CO2e greenhouse gas emissions would decrease from an estimated 254 million kg to 48 million kg per year within the North-Central U.S. (assuming again that 30 million hectares are planted to soybeans in this region). This implies that the action of natural enemies of aphids coupled with the use of a spray threshold reduces greenhouse gas emissions by approximately 207 million kg of CO2e per year.
Discussion
We estimated emissions of 10.6 kg CO2 equivalent greenhouse gasses per hectare of soybeans sprayed with insecticides against the soybean aphid, an insect pest native to Asia that invaded North America in the year 2000. These values are similar to estimates for emissions associated with insecticide use by other authors [22,23]. Since the invasion of soybean aphid, insecticide use in soybeans in the North-Central United States has increased from less than 25,000 hectares per year prior to 2001 to levels approaching 4 million hectares in 2006. The USDA NASS database estimates that insecticides have been used against soybean aphid on a total of 8.32 million hectares during the years 2001, 2002, 2004, 2005, and 2006 (data for other years following the soybean aphid invasion are not available). Our estimate of GHG emissions attributable to insecticide use directed at soybean aphid for these years in the United States is therefore 87.2 million kg CO2e, or an average of 17.4 million kg CO2e greenhouse gases per year during this period. As a point of reference, this annual amount of emissions is equivalent to CO2e produced by the burning of approximately 7.4 million liters of gasoline, and could be offset by CO2 sequestration achieved by approximately 5,800 hectares of U.S. forest land per year (U.S. E. PA. Greenhouse Gas Equivalencies Calculator; updated Oct. 2012; http://www.epa.gov/cleanenergy/energy-resources/calculator.html).
The magnitude of these emissions would be far greater were it not for biological control of the soybean aphid, and an economic spray threshold that allows farmers to take advantage of biological control and other factors that limit soybean aphid populations. Using existing data [30,52] we estimated that the spray threshold reduced potential emissions as much as 300 million kg CO2e greenhouse gases per year and that reductions of emissions due to biological control maintaining aphid densities below the threshold at over 200 million kg CO2e. This amount of emissions reduction is equivalent burning approximately 88 million liters of gasoline or to sequestration achieved by 68,700 hectares of U.S. forest land (U.S. E.P.A. Greenhous Gas Equivalencies Calculator). While a number of economic and ecological benefits have been attributed to biological control [53–57], this is the first consideration of benefits accruing through reduction of greenhouse gas emissions.
Our estimate of emissions attributable to soybean aphid management is conservative for a number of reasons. First, our per-hectare estimates of insecticide manufacture underestimate emissions because only the active ingredient is included. Additives such as adjuvants are not included in the USDA NASS estimates of kg of insecticide use. We also do not include emissions associated with the use of insecticides applied as seed treatments, which are primarily the neonicotinoids. One estimate from 2010 was that 20% of soybean seeds on the market contained a neonicotinoid seed treatment, but this is increasing [58]. Greenhouse gas emissions associated with seed treatments are exclusively due to manufacturing costs because post-planting application is avoided, but our analysis showed that the energy required to manufacture insecticides can exceed the energy used to apply them. Another source of GHG emissions not included involves the manufacture and maintenance of specialized equipment for insecticide application against soybean aphid. It does appear that many growers purchased a sprayer specifically for use against soybean aphid [26] and the associated emissions could reasonably be added to our overall estimate. However, this equipment could have other uses, notably for fungicide applications [59], so we have omitted this source of emissions from our analysis. Lastly, due to data collection limitations our estimate of total emissions does not include the years 2003, 2007 or 2008, which were characterized by high soybean aphid densities in at least parts of the region [59,60].
Many pest management tactics that reduce the need to apply foliar insecticides have the potential to further reduce greenhouse gas emissions. Three tactics with potential for such effects are (i) host plant resistance, (ii) cultural control methods, and (iii) classical biological control. Soybean varieties that exhibit resistance to soybean aphid have been developed and have the potential to greatly reduce insecticide use [18]. A caveat is that strains (“biotypes”) of soybean aphids have been found that are able to develop normally on resistant soybean cultivars [20]. Cultural control methods against the soybean aphid are based on the observation that biological control can be enhanced by habitat diversification ( [30,61] but see 51,62) These methods can include cover cropping strategies that reduce pest pressure [63–65] and thus the need to apply insecticides, but may also increase some emissions through increased cultivation or planting. Classical biological control, in which exotic natural enemies of soybean aphid are imported from its native range could reduce or even eliminate the need to apply insecticides if successful [19]. To date however, no classical biological control has been successfully established [18,66,67].
We have used information on insecticide applications against the soybean aphid in the United States to show that invasive species can lead to significant greenhouse gas emissions that would not have occurred in the absence of the invasion. Invasive species are expected to have implications for the carbon cycle beyond pesticide use, however, and these include effects on other management strategies. For example, bacterial nitrogen fixation in soybeans is reduced by soybean aphid infestation [68], which could lead to increased nitrogen fertilizer inputs and attendant greenhouse gas emissions. Invasive species can also decrease carbon sequestration by plants as has been shown for bark beetles [17]. Other effects on sequestration are possible as well, depending upon the ecological effects of the invading species. Our analysis highlights the fact that invasive pest species are not only affected by global climate change, but they can also affect it – in this case by increasing the greenhouse gas emissions associated with management tactics.
Acknowledgments
We thank Bill Lazarus for fruitful discussion, and Nicolas Desneux, Jonathan Dregni, Jon Foley, Matt Kaiser, Doug Landis, Kimberly Mullins and an anonymous reviewer for comments on the manuscript.
Author Contributions
Conceived and designed the experiments: GEH JDH YY. Performed the experiments: JDH YY. Analyzed the data: JDH YY GEH. Wrote the manuscript: GEH JH DWR.
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