Using soil sensing technology to examine interactions and controls between ectomycorrhizal growth and environmental factors on soil CO2 dynamics
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- Hasselquist, N.J., Vargas, R. & Allen, M.F. Plant Soil (2010) 331: 17. doi:10.1007/s11104-009-0183-y
Soils play a critical role in the global carbon cycle, yet the biophysical factors regulating soil CO2 dynamics remain unclear. We combined high-frequency in situ observations of fine roots and ectomycorrhizal (EM) fungi with data from multiple soil sensor arrays to examine the biophysical interactions influencing soil CO2 production for one year in a mixed conifer forest. Using structural equation modeling we constructed a hypothesized model to test for causal interactions among environmental factors, biotic factors, and soil CO2 dynamics throughout the soil profile. According to our model, seasonal variation in CO2 production was significantly influenced by EM rhizomorph production, soil temperature, and soil moisture. Fine root production, on the other hand, did not appear to significantly influence soil CO2 production. The relationship between EM rhizomorph production and soil CO2 production was also supported by a zero temporal lag between these two measurements in a cross-correlation analysis. In contrast, CO2 production increased before fine root production suggesting that these two measurements were decoupled in time. Results from this study highlight the need to better understand differences in carbon allocation between plant roots and EM fungi to improve our predictions of soil carbon dynamics under global climate change.
KeywordsEctomycorrhizal rhizomorphs Fine roots Minirhizotron Soil CO2 production Soil sensors Structural equation model
Soils are of particular importance in the global carbon cycle because they contain more carbon than live biomass (Eswaran et al. 1993), and the efflux of CO2 from the soil surface (Rs) represents a major flux of carbon into the atmosphere (Raich and Schlesinger 1992, Schlesinger and Andrews 2000). Previously, Rs has been reported to represent 40–80% of total ecosystem respiration (Law et al. 1999, Janssens et al. 2001). It is therefore crucial to understand the biotic factors influencing Rs as well as how these factors are affected by seasonal changes in environmental conditions in order to accurately estimate Rs. However, understanding the interactions between environmental factors, biotic factors, and Rs is complex and involves the product of numerous biophysical interactions (Stoyan et al. 2000, Davidson et al. 2006). In this study, we combined in situ observations of fine roots and ectomycorrhizal (EM) fungi with continuous data from multiple soil sensor arrays (Allen et al. 2007) in order to examine the interactions between environmental factors, biotic factors, and CO2 dynamics throughout the soil profile.
The importance of biotic factors for Rs has frequently been divided between autotrophic respiration (generally referred to as root respiration) and heterotrophic respiration (respiration from decomposers). Roots are the primary belowground structural element of plants and have previously been reported as major factors influencing the autotrophic component of Rs (Ewel et al. 1987, Edwards 1991, Bowden et al. 1993, Boone et al. 1998). Autotrophic respiration can account for as little as 10% or greater than 90% of total in situ Rs depending on vegetation type and season of the year (Hanson et al. 2000). However, autotrophic respiration is not limited to plant roots. Within hours, recently fixed carbon is transported to EM fungi (Söderström and Read 1987, Högberg et al. 2008), the symbiotic associates of woody plants. Consequently, autotrophic respiration should be considered as a combination of both root respiration and EM fungal respiration. Difficulties in separating root respiration from fungal respiration have resulted in EM fungal respiration being included with root respiration, and only recently have researchers begun to separate and identify the importance of EM fungi for Rs (Fahey et al. 2005, Langley et al. 2005, Heinemeyer et al. 2007, Vargas and Allen 2008a, b). For example, Heinemeyer et al. (2007) used a mycorrhizal mesh collar design and found that EM hyphae contributed ~ 25% to Rs in a lodgepole pine forest.
Ectomycorrhizal fungi are the dominant mycorrhizal partners in boreal and north temperate forests, mediating the flux of nutrients and water from soils to their host plants in exchange for host carbohydrates (Read 1991). The vast majority of nutrient-absorbing surface area for plants in these regions resides with EM fungi, and up to 20% of net primary production is estimated to flow through EM fungi to maintain this surface area (Treseder and Allen 2000). The morphology of EM hyphae is often complex, ranging from individual hyphae to cords that form rhizomorphs and act like vessel elements in plants, transporting water for distances up to several meters (Duddridge et al. 1980). In semi-arid mixed conifer forests, such as our research site, EM associations might be extremely important because EM rhizomorphs can extend several meters into the surrounding soil matrix in search for patches of nutrients and water otherwise unavailable to non-mycorrhizal plants (Allen 2007). Although recent studies have shown the importance of fine roots and EM fungi for Rs (Fahey et al. 2005, Langley et al. 2005, Heinemeyer et al. 2007, Vargas and Allen 2008a, b), we still do not have a good mechanistic understanding of the biophysical interactions influencing CO2 dynamics throughout the soil profile.
Recent developments in automated measurements of Rs are generating increasing numbers of high temporal-resolution observations (Savage and Davidson 2003, Allen et al. 2007, Carbone and Vargas 2008), which in turn present the opportunity to move towards a more predictive understanding of the key mechanisms influencing Rs. Researchers are now able to continuously monitor CO2 concentrations at multiple soil depths (Hirano et al. 2003) as well as calculate CO2 production throughout the soil profile (Davidson and Trumbore 1995, Risk et al. 2002, Vargas and Allen 2008c). The understanding of changes in soil CO2 concentrations is important for soil CO2 dynamics because changes in CO2 concentrations influence soil CO2 production as well as Rs (Simunek and Suarez 1993). Along with continuous measurements of soil CO2, it is just as critical to incorporate frequent observations of fine root and EM fungal dynamics (Misson et al. 2006, Vargas and Allen 2008a, Stewart and Frank 2008). Fine root and EM rhizomorphs rapidly respond to climatic events (Heinemeyer et al. 2007, Vargas and Allen 2008a), and as a result it is important to understand how their dynamics might influence CO2 concentrations throughout the soil profile. Therefore, measurements of fine root and EM rhizomorph dynamics, soil CO2 and environmental factors should be undertaken on similar temporal scales to better understand the biophysical interactions influencing soil CO2 dynamics.
In this study, although we estimate Rs, we focused on developing models to predict CO2 production because it provides a more desirable indicator of the biological activity in the soil, whereas the efflux of CO2 from the soil surface includes complex parameters describing the interface between soil and the atmosphere (Chen et al. 2005). Furthermore, it is difficult to relate a specific depth of soil temperature when developing models to predict Rs, but when developing models to predict soil CO2 production we can use the temperature at the depth which soil CO2 production was calculated using the gradient flux method (Simunek and Suarez 1993). Here, we combined high frequency observations from minirhizotron images with data from an array of soil sensors to examine relationships between environmental factors (photosynthetically active radiation (PAR), soil temperature and moisture), biotic factors (production of fine roots and EM rhizomorphs), and soil CO2 dynamics (CO2 production and CO2 concentrations) in a mixed conifer forest. By using minirhizotron cameras we were able to non-destructively observe in situ root and EM rhizomorph dynamics throughout the soil profile as described in previous studies (Hendrick and Pregitzer 1996, Johnson et al. 2001, Treseder et al. 2005). Additionally, the field site has an array of environmental soil sensors collecting continuous data at multiple depths (see Allen et al. 2007). Using structural equation modeling we constructed a hypothesized model to test causal relationships among environmental factors, biotic factors, and soil CO2 dynamics without disturbing the environment (Ullman 2001). Our objectives were: 1) to determine how seasonal changes in environmental factors affect fine root and EM rhizomorph production; and 2) to determine the relative importance of fine root and EM rhizomorph production on seasonal variation in soil CO2 concentrations and CO2 production throughout the soil profile. We hypothesized that the production of soil CO2 is more tightly coupled to EM rhizomorph production than the production of fine roots. This hypothesis is supported by the fact that soil CO2 dynamics and EM rhizomorph production are strongly influenced by rapid changes in soil temperature and moisture (Heinemeyer et al. 2007, Vargas and Allen 2008a), whereas fine root production respond slower to changes in environmental conditions because of the greater carbon and nutrient costs associated with the production of fine roots (Smith and Read 1997).
Materials and methods
The study was conducted at the University of California James San Jacinto Mountain Reserve, a Natural Reserve System field station of the University of California (www.jamesreserve.edu). The Reserve is a mixed conifer forest at 1640 m in the San Jacinto Mountains, California, USA. Most of the precipitation occurs between November and April; with a mean annual precipitation of 640 mm. Dominant trees at our site include Quercus kelloggii Newb. (California black oak), Pinus lambertiana Dougl. (Sugar Pine) and Arctostaphylos pringlei Parry (Manzanita). The Reserve has served as the Terrestrial Ecology Observing Systems field site for the Center for Embedded Networked Sensing (CENS, http://research.cens.ucla.edu) with the goals to research and develop new environmental sensing technologies for ecological observations (Allen et al. 2007, Hamilton et al. 2007).
Image collection and analysis
In October 2003, we installed an array of six minirhizotron tubes, 5 cm in diameter and 1 m long, in a 40 m2 area as described in Vargas and Allen (2008a). We allowed roots and EM rhizomorphs to recolonize the soil surrounding the tubes for two years before images were collected. The images were collected using a minirhizotron microscope (BTC-10 and I-cap software, Bartz Technology) fitted to a laptop computer. Images from all tubes were collected in weekly campaigns between February 2006 and February 2007, with a total of 59 sampling dates or “minirhizotron sessions” at intervals that varied from one day to one month. On average we collected 52 vertical images per tube by inserting the minirhizotron until it reached the bottom of the tube and then moved the camera upward at increments of 1.3 cm. A total of 313 images were collected per day and stored as JPEG files. This high sampling frequency between “minirhizotron sessions” is critical for examining fine root and EM fungal dynamics (Stewart and Frank 2008, Vargas and Allen 2008a).
Images from the minirhizotron camera provided good resolution to accurately identify fine roots, EM root tips (Majdi and Nylund 1996) and EM rhizomorphs (Treseder et al. 2005). Ectomycorrhizal rhizomorphs were identified morphologically, as angular-branching, filamentous structures emanating from EM root tips. Additionally, most rhizomorphic fungi located in the mineral soil tend to be ectomycorrhizal, not saprobic (Dickie et al. 2002), and molecular characterization of rhizomorphic fungi at our study site indicates that these fungi are known EM species (Glass and Allen, unpublished data). For each minirhizotron tube, fine root and EM rhizomorph production was determined for each day images were taken as the number of newly appearing roots and rhizomorphs, similar to how Majdi and Nylund (1996) classified “new” roots. We chose only fine root and EM rhizomorph production because these structures are likely to be metabolically active and therefore influence soil CO2 concentrations and in turn soil CO2 production. However, we are aware that persistent roots and EM rhizomorphs also contribute to CO2 production through basal metabolism, and therefore our results may underestimate the importance of fine roots and EM rhizomorphs on soil CO2 dynamics.
Micrometeorological data and soil CO2
In November 2004, we deployed four soil sensor arrays within our 40 m2 study area as described in Allen et al. (2007). Each soil sensor array consisted of a suite of environmental sensors placed at three depths (2, 8, 16 cm). At each depth we measured soil temperature, soil moisture (ECHO, Decagon Inc.) and CO2 concentrations using solid-state CO2 sensors (CARBOCAP model GMT 220, Vaisala, Finland). In addition, we measured photosynthetically active radiation (PAR) at a height of 2 m (S-LIA-M003, Onset Computer Corporation, Bourne, Massachusetts, USA). All environmental variables were recorded at five minute intervals.
Root production, EM rhizomorph production, and environmental data were subjected to a non-parametric Mann–Whitney U test to determine significant differences (α < 0.05) between the growing season (April–August) and the rest of the year. Aboveground CO2 assimilation rates at our study site are significantly higher between April and August compared to the rest of the year (Goode and Allen, unpublished data). Furthermore, this time period of high carbon assimilation corresponds to when oaks in California are photosynthesizing (Ma et al. 2007). We therefore wanted to look at seasonal differences between the growing season (April–August) and the rest of the year.
Because of the time intervals between minirhizotron images, we are uncertain about the exact dates of root and rhizomorph production. We therefore examined different running averages in the environmental data to determine the best correlation between root and rhizomorph production and environmental data. Pearson correlation coefficients were calculated and compared to determine the best running average for the environmental data. Averages included (a) mean daily averages for the same date minirhizotron images were taken (Ti), (b) the mean daily average of Ti and the day before the minirhizotron images were taken (TA1 = (Ti + Ti-1/2)), (c) the mean daily average between Ti and two days before the minirhizotron images were taken (TA2 = (Ti + Ti-1 + Ti-2/3)), and (d) the mean daily average between Ti and three days before the minirhizotron images were taken (TA3 = (Ti + Ti-1 + Ti-2 + Ti-3/4)). Statistical analyses were performed using JMP Version 3.2.2 (SAS Institute, Cary, North Carolina, USA).
Cross-correlation analyses were used to identify time-lag effects between EM rhizomorph or fine root production and soil CO2 production using MATLAB R2007a (The MathWorks Inc., Natik, Massachusetts, USA). Cross-correlation analysis is a measure of similarity between two different measurements as a function of a time-lag applied to one of them (Nielsen and Wendroth 2003). Therefore, by using this type of analysis we were able to investigate temporal relationships between changes in EM rhizomorph or fine root production and soil CO2 production. We performed these analyses with daily mean values for each one of the measurement days (minirhizotron sessions) of the mentioned variables.
We also observed seasonal variation in environmental factors during the study (Fig. 2a, b). Mean daily PAR values ranged from a low of 11 µmol/m2s to a high 405 µmol/m2s (Fig. 2a) and were nearly twice as great during the growing season (305. 7 ± 6.7 µmol/m2s compared to 165.7 ± 5.3 µmol/m2s, respectively; χ 2 = 158.8, df = 1, P < 0.001). Mean daily soil temperatures at 8 cm were significantly higher during the growing season compared to the rest of the year (16.6 ± 0.4°C and 7.7 ± 0.3°C, respectively; χ 2 154.3, df = 1, P < 0.001). Soil temperatures did not start increasing until the last week in April and after four months of continuous increase, soil temperatures peaked in late August (24.7°C) and gradually declined during the fall months (Fig. 2b). We observed two peaks in soil temperature during the winter months; one in early January (8–11) and the other in early February 2007 (10–17). Soil moisture at 8 cm was not significantly different between the growing season and the rest of the year (χ 2 = 1.6, df = 1, P = .21) and averaged 10.75%. On August 17, our field site experienced a significant monsoon rain event, which accounted for the observed pulse in soil moisture (Fig. 2b).
When comparing correlation coefficients using different running averages in the environmental data, we found that the highest overall coefficients were from the running average of two days before minirhizotron images were taken (TA2). We therefore used this running average (TA2) for all environmental data in subsequent structural equation modeling (SEM) analysis. In contrast, the mean daily averages of environmental data corresponding to the same date minirhizotron images were taken (Ti) had the lowest overall correlation coefficients.
At 8 cm depth, our model passed the goodness-of-fit test (χ 2 = 2.96; P = 0.09; Fig. 4b), with variation inflation factors up to 4.6 and condition indices up to 13.7. At this depth, 81% of the variation in CO2 concentrations was explained by the model with direct positive effects from EM rhizomorph production, soil moisture, and soil temperature. Our model also accounted for 45% of the variation in EM rhizomorph production with direct positive effects from both soil temperature and fine root production. In contrast, only 21% of the variation in fine root production was explained at this depth with a direct positive effect from PAR (Fig. 4b).
At 16 cm depth, the observed and expected correlation matrices did not differ significantly (χ 2 = 2.85; P = 0.09; Fig. 4c), with variation inflation factors up to 4.2 and condition indices up to 13.5. According to our model, we could account for 76% of the variation in CO2 concentration with direct positive effects from EM rhizomorph production, soil moisture, and soil temperature. At this depth, our model explained 28% of the variation in EM rhizomorph production with direct positive effects from both soil temperature and fine root production. In contrast, only 6% of the variation in fine root production was explained at this depth with no significant direct effects from the environmental factors (Fig. 4c).
We used the same hypothesized model and tested for causal relationships between environmental factors and biotic factors on soil CO2 production. The observed and expected correlation matrices did not differ significantly (χ 2 = 2.21; P = 0.14), indicating that the model was a good fit (Fig. 4d). According to our model, 61% of the variation in soil CO2 production could be explained by direct positive effects from EM rhizomorph production, soil temperature, and soil moisture (Fig. 4d). In addition to directly affecting CO2 production, soil temperature also indirectly affected CO2 production through its interaction on EM rhizomorph production. Fine root production did not significantly affect soil CO2 production. The biggest variance inflation factor (4.2) was well below the critical limit of 10 and the biggest condition index (13.2) was well below the critical limit of 30 (Petraitis et al. 1996).
In this study we used soil sensing technology to non-destructively examine the biophysical interactions influencing seasonal soil CO2 dynamics in a mixed conifer forest. During the study there was considerable variation in both soil CO2 production (P i ) and Rs (Fig. 3b), with significantly higher rates during the growing season compared to the rest of the year. Previous studies have also reported seasonal patterns in Rs and attributed increased rates of Rs in spring to seasonal variation in photosynthesis and increased rates of autotrophic (root) respiration (Raich and Tufekciogul 2000, Janssens et al. 2001, Baldocchi et al. 2006). However, in this study increased rates of soil CO2 production (P i ) at 8 cm depth during the growing season correlated with periods of high EM rhizomorph production, whereas fine root production did not appear to significantly affect soil CO2 production. When comparing the total effects of EM rhizomorph production, soil temperature and soil moisture on soil CO2 production we found that EM rhizomorph production accounted for ~ 15% of the variation in CO2 production in our model (Fig. 4d), which is consistent with a recent study by Fahey et al. (2005) where the authors used an indirect mass balance approach and estimated that mycorrhizal fungi accounted for ~ 12% of Rs in a hardwood forest.
The allocation of carbon between fine roots and mycorrhizal fungi is often dependent on environmental conditions. In semi-arid environments such as our research site, water is often limiting for plant growth and therefore carbon investment in mycorrhizal fungi may be favored because of their ability to access water and nutrients from the smaller micropores in the soil that are otherwise inaccessible to plant roots (Allen 2007). Throughout this study we observed three times more EM rhizomorphs than roots (Fig. 2a), indicating a substantial carbon investment in EM fungi. Investment in EM fungi was especially pronounced in May, shortly after the leafing out of oaks, as well as in August when temperatures were at their highest and at the same time our study site experienced a significant rain event (Fig. 2). Previously, Vargas and Allen (2008b) reported a seasonal hysteresis effect for Rs at this study site, with higher rates during the growing season when temperatures were increasing and soil moisture was high. They hypothesized that one plausible explanation for the seasonal hysteresis effect may be due to differences in the relative contributions of growth respiration and maintenance respiration in the autotrophic contribution of Rs. Results from our study showed significantly higher rates of EM rhizomorph production during the growing season as well as a positive correlation between soil temperature and EM rhizomorph production. Therefore, respiration associated with EM rhizomorph production may, in part, help explain the seasonal hysteresis effect previous observed by Vargas and Allen (2008b).
Overall, our model explained between 70% and 81% of the variation in CO2 concentrations throughout the soil profile (Fig. 4). At both 8 cm and 16 cm depth, variation in CO2 concentrations was significantly influenced by EM rhizomorph production, soil moisture, and soil temperature. In contrast, variation in CO2 concentrations at 2 cm depth was significantly influenced by only soil moisture and soil temperature (Fig. 4a). The lack of correlation between biotic factors and CO2 concentrations at 2 cm depth may be the result of other physical parameters near the soil surface, such as changes in wind patterns and CO2 diffusivity as well as unmeasured biotic factors, such as the activity of fine hyphae and bacteria that influence soil CO2 concentration. In this study, we restricted our definition of biotic factors to the production of fine roots and EM rhizomorphs because these structures can be easily observed using the Bartz minirhizotron camera. However, much of the biomass in the upper layer of the soil profile is composed of decomposers (Glass and Allen, unpublished data) that contribute to the heterotrophic respiration component of Rs. A large contribution from heterotrophic respiration may therefore be responsible for the lack of correlation between biotic factors and CO2 concentrations at 2 cm depth. Further studies combining automated measurements of soil CO2 production, fine roots, EM rhizomorphs, and destructive microbial measurements are needed to better tease apart the relative contributions from the different components of Rs at this depth.
Throughout the study, we observed four peaks in soil CO2 production (Fig. 3b). The first two peaks occurred during the growing season and corresponded to dates with the highest EM rhizomorph production, suggesting a rapid response of EM fungi to pulse rain events. This supports earlier findings by Pigott (1982) that certain EM fungi can withstand desiccation in an inactive state, making them ready to respond quickly to rewetting events. Additionally, EM rhizomorphs can be maintained through dry periods by hydraulically-redistributed water (Querejeta et al. 2003, 2007, 2009), in which EM fungi associated with hosts performing hydraulic lift receive water from their host tree, and transfer this water to mycelium and rhizomorphs. These results also have implications for our understanding of pulses in soil CO2 production as well as Rs. These pulses have been identified as a burst of decomposition of organic compounds and release of inorganic nitrogen by the rewetting of soils that have been dry for a long period and has been termed the “Birch effect” (Jarvis et al. 2007). This effect is primarily controlled by heterotrophic activity, but our results suggest that autotrophic respiration may also contribute to the “Birch effect” via the rapid production of EM rhizomorphs during these rewetting events. More research is needed to elucidate the potential role of rapid EM rhizomorph production and their contribution to Rs during rain pulse events.
The other two peaks in CO2 production occurred in January and February of 2007 (Fig. 3b), corresponding to times with very little fine root and EM rhizomorph production. Both peaks in 2007 correspond to times of relatively high soil moisture combined with pulses of increased soil temperature. One plausible explanation for these peaks may be due to quick response of heterotrophic respiration to sudden increases in soil temperature under no water limitation, which is consistent with the well recognized exponential relationship between heterotrophic respiration and temperature (Hanson et al. 2000).
The relative importance of fine roots and EM fungi on soil CO2 dynamics may be underestimated in this study because we only considered respiration costs associated with the production of new roots and rhizomorphs. Soil CO2 production is also a function of basal metabolism, in addition to the respiration costs of new roots and rhizomorphs. According to our model, fine root production did not significantly affect soil CO2 production, but that does not imply that plant roots do not contribute to soil CO2 production. Instead, the lack of measurable change in root production may indicate that roots are investing in basal metabolism in order to maintain active roots. On the other hand, the smaller biomass and shorter lifespan of EM rhizomorphs could mean that there is minimal basal metabolism without production. Therefore, the production of soil CO2 could be tightly coupled to EM rhizomorph production, but not necessarily coupled to the production of new roots. This difference between basal metabolism and respiration costs associated with production of fine roots and EM rhizomorphs may, in part, help explain the discrepancies between our results and previous results at our study site. Previously, Vargas and Allen (2008a, b) used fine root and EM rhizomorph lengths, which takes into account the respiration costs associated with maintaining functional roots and rhizomorphs (i.e. basal metabolism), and found a positive correlation between fine roots and Rs. Further research is needed to differentiate the respiration costs associated with fine root and EM rhizomorph production versus basal metabolic activity of these structures in regulating soil CO2 dynamics.
The unique aspect of this study was combining high frequency observations of fine root and EM rhizomorph production with data from an array of soil sensors to non-destructively examine the biophysical interactions influencing soil CO2 dynamics. Based on in situ observations, our results showed that increased rates of soil CO2 production were correlated with increased rates of EM rhizomorph production, but not necessarily correlated with fine root production. The difference in carbon allocation between plant roots and EM fungi may have significant consequences to our predictions of soil carbon balance under global climate change. For example, plants are likely to become more nutrient- and water-limited under elevated atmospheric CO2 conditions, rather than carbon-limited, and as a result more carbon may be allocated to EM fungi (Allen et al. 2005). Ectomycorrhizal fungi have shorter lifespans than plant roots, and as a result EM fungi may represent what Heinemeyer et al. (2007) described as a CO2 “overflow tap.” In this scenario, surplus carbon invested in EM fungi is quickly returned to the atmosphere, thereby limiting expected carbon sequestration under elevated CO2 conditions. Our results support a number of recent studies (Fitter et al. 2000, Treseder and Allen 2000, Alberton et al. 2005) calling for more understanding of the role of mycorrhizal fungi in carbon cycling, and highlight the need to better understand the complex interactions between environmental factors, mycorrhizal fungi, and their contribution to the global carbon cycle (Allen et al. 2007).
We thank Hector Estrada, Laurel Salzman, Ayesha Sirajuddin, and William Swenson for their help acquiring minirhizotron images. Chris Glover and Kuni Kitajima helped in processing the images. Mike Taggart and Tom Unwin helped on the installation of power supply for our system and maintain the sensor infrastructure. This research was undertaken with funding from the National Science Foundation (grant no. EF-0410408), the Center for Embedded Networked Sensing (grant no. CCR-0120778), and the Kearney Foundation. RV was supported by grant DEB-0639235 while writing this manuscript. The authors would like to thank Darrel Jenerette for useful comments on a previous draft of this work.
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