Potential for atmospheric deposition of bacteria to influence bacterioplankton communities

Authors

  • Stuart E. Jones,

    1. Limnology and Marine Sciences Program, University of Wisconsin-Madison, Madison, WI
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  • Ryan J. Newton,

    1. Microbial Doctoral Training Program, University of Wisconsin-Madison, Madison, WI, USA
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  • Katherine D. McMahon

    1. Limnology and Marine Sciences Program, University of Wisconsin-Madison, Madison, WI
    2. Microbial Doctoral Training Program, University of Wisconsin-Madison, Madison, WI, USA
    3. Department of Civil and Environmental Engineering, University of Wisconsin-Madison, Madison, WI, USA
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  • Editor: Riks Laanbroek

Correspondence: Katherine D. McMahon, 1415 Engineering Drive, Madison, WI 53706. Tel.: +1 608 263 3137; fax: +1 608 262 5199; e-mail: tmcmahon@engr.wisc.edu

Abstract

Biogeographic patterns in microbial communities are an exciting but controversial topic in microbial ecology. Advances in theory pertaining to assembly of microbial communities have made strong assumptions about dispersal of bacteria without exploration. For this reason, we investigated rates of atmospheric bacterial deposition and compared the taxonomic composition of bacteria in rain with that of common freshwater bacterial communities. Our findings suggest that it is not appropriate to take for granted that atmospheric deposition of bacteria is a significant vector of immigration to freshwater ecosystems.

Introduction

The field of microbial ecology is experiencing a period of rapid advancement in its ability to use theoretical frameworks to study and explain the distribution, abundance, and dynamics of microbial taxa. Microbial ecologists are successfully applying traditional ecological concepts to bacterial communities; examples include island biogeography (MacArthur & Wilson, 1967; Whitaker et al., 2003; Horner-Devine et al., 2004), the neutral theory of biodiversity (Bell, 2000; Hubbell, 2001; Sloan et al., 2006; Woodcock et al., 2007), and local-regional diversity scaling (Fenchel et al., 1997; Fenchel & Finlay, 2004; He et al., 2005). The application of these conceptual models is encouraging to those hoping to quantitatively predict or model bacterial community assembly. However, many of these open-system theories make assumptions about, or estimate parameters describing, immigration rates and the composition of the regional community (Martiny et al., 2006; Sloan et al., 2006; Woodcock et al., 2007). For example, application of the neutral theory framework to bacterial communities (Sloan et al., 2006) requires estimation of the relative composition of the ‘source community’ from observation and an immigration parameter (m). m is the probability that a death in the local community is replaced by an immigrant from the source community and therefore 1−m is the probability that a death in the local community is replaced from within. In addition, very few efforts have been made to estimate the taxonomic composition of bacteria immigrating into ecosystems or the relative significance of immigration for community assembly processes.

Rates of immigration and the taxonomic identity of immigrants entering lakes by surface water flow have been reported previously (Lindstrom & Bergstrom, 2004; Lindstrom et al., 2006). As might be expected, hydraulic residence time plays a key role in determining the similarity between the inlet and lake bacterial community composition and the relative contribution of the inlet to the cell concentration in the recipient lakes (Lindstrom & Bergstrom, 2004; Lindstrom et al., 2006). Hydrology seems to play a similar role in determining bacterial abundance and composition in estuarine systems (Crump et al., 2004). These studies indicate that connectivity between physically distinct aquatic environments can influence the bacterial community in the recipient ecosystem. However, the majority of bacterial taxa observed in these studies have been observed previously in aquatic environments (Crump et al., 2004; Lindstrom & Bergstrom, 2004; Lindstrom et al., 2006). We hypothesize that the number and composition of bacteria depositing into aquatic systems from the atmosphere differs from the number and composition immigrating via surface water inflow.

Information about atmospheric transport of bacterial cells in the literature is derived mainly from research conducted in agricultural systems (Lindemann et al., 1982; Lindemann & Upper, 1985; Lindow & Andersen, 1996). The majority of this research sought to understand the release mechanisms of bacterial and fungal plant pathogens to the atmosphere, and drivers of subsequent deposition on fields (Lindemann & Upper, 1985; Lindow & Andersen, 1996). All of this work relied on culture-dependent microbiological techniques, such as enumeration of CFUs. A few studies have since used molecular techniques to identify the taxonomic composition of bacteria in the lower atmosphere (Brodie et al., 2007). In the studies that have used these techniques (Maron et al., 2005; Ahern et al., 2007; Brodie et al., 2007), the fate of the atmospherically deposited organisms either were not considered or were primarily considered in relation to public health issues.

The current study represents an investigation of the potential for airborne bacteria to affect aquatic bacterial community composition. This question is also more broadly relevant to molecular, microbial ecologists who consider ecological questions such as those outlined above.

Materials and methods

Sampling of atmospheric deposition

Dry and wet deposition of bacterial cells were sampled using 25-cm-diameter dust collectors containing 250 mL of 10% formaldehyde in glycerol (Segawa et al., 2005). Four dust collectors were deployed on each of the surfaces of five northern Wisconsin lakes, two in littoral areas (near shore) and two in pelagic areas (near geographic center) for 8 days. All lakes were within 2 km of the University of Wisconsin's Trout Lake Field Station (46°01′N, 89°40′W); land use in this region is primarily national forest and seasonal residence. Subsamples (10 mL) were collected from dust collectors at c. 0, 48, 96, and 192 h after deployment (July 11, 2006 to July 19, 2006) using a sterile pipet and were stored in scintillation vials at room temperature until bacteria could be enumerated using 4′,6′-diamidino-2-phenylindole (DAPI). A small amount (3.3 mm) of precipitation occurred over the 8-day period. The first hour of precipitation (6.0 mm) during a rainstorm on July 23, 2006 was also collected using sterilized dust collectors, but the need for rapid deployment and retrieval necessitated deployment at Trout Lake Field Station. For collection of rainwater, two dust collectors were deployed at each of two sites, located c. 200 m apart. The forest canopy at one site was dominated by deciduous trees and the canopy at the second site was dominated by conifers. A sample of rain was also stored for subsequent enumeration of bacterial cells. The rain samples from July 23, 2006 and the contents of dust collectors following 192 h of dry deposition deployment were collected on 0.2 μm Supor-200 filters (Pall) and stored at −80 °C until DNA extraction with a FastPrep Spin DNA purification kit (Qbiogene) and previously described modifications (Kent et al., 2004).

Calculation of deposition rates

Dust collector subsamples were incubated with DAPI (100 ng mL−1, final concentration) and collected onto 0.2-μm polycarbonate filters (Millipore) (Porter & Feig, 1980). Ten digital pictures of each filter were taken using a Zeiss Axioplan 2 compound microscope equipped with an Olympus DP70 camera. Cells were enumerated using IP Lab v3.71 (Scanalytics Inc.) segment enumeration tools. Rates of deposition per square meter per hour were calculated as the change in concentration of cells in subsamples multiplied by the volume of the dust collector (measured after 192 h deployment) and divided by the time since last sampling and area of the dust collector.

Clone library construction, sequencing, and analysis

16S rRNA gene clone libraries were constructed from rain samples at the deciduous- and conifer-dominated sites. The fixative placed in dust collectors used to estimate dry deposition rates dramatically decreased the PCR detection limit (>3 orders of magnitude, data not shown), and therefore clone libraries could not be constructed from dry deposition samples. Methods used for clone library construction were published elsewhere (Newton et al., 2006). Briefly, we amplified bacterial 16S rRNA genes and their corresponding 16S–23S internal transcribed spacer (ITS) region from DNA using a 20-cycle PCR reaction (Eppendorf Mastercycler) with previously described conditions (Newton et al., 2006). Clone libraries were constructed for each of the rain samples using standard protocols from the Invitrogen Topo TA Cloning® system with TOP10 chemically competent cells and sequenced using the ABI Prism BigDye terminator sequencing kit (PE Applied Biosystems). A single sequencing pass using the 1492R primer (5′-GGTTACCTTGTTACGACTT-3′) was conducted to determine the approximate phylogenetic affiliation of each clone. Sequences were checked for putative chimeras using the program mallard (Ashelford et al., 2006), but none were identified. Our rain library was appropriately sampled at c. 92% sequence identity based on the full bias corrected chao 1, ace, and bootstrap-based richness estimators (Schloss & Handelsman, 2005).

In order to compare bacterial taxonomic composition of aquatic systems, the atmosphere, and our rain samples, we compiled previously published 16S rRNA gene sequences from freshwater (Zwart et al., 2002; Newton et al., 2006) and atmospheric samples collected at an urban site in Texas (Brodie et al., 2007) and in rural France (Maron et al., 2005). The review of freshwater bacterial diversity by Zwart et al. (2002) included all available 16S rRNA gene sequences from freshwater systems available at the time of publication and is the most current, published metaanalysis of freshwater bacterial 16S rRNA gene sequences. Newton et al. (2006) have since conducted a survey of bacterial 16S rRNA gene sequences across the 2002 ice off-season in one of the lakes included in this study (Crystal Bog). The Brodie et al. (2007) and Maron et al. (2005) 16S rRNA gene sequences were collected from a sample of air from San Antonio in July of 2003 and rural France in March and May of 2003, respectively. Although collected at disparate times and locations, this collection of sequences is expected to represent bacterial 16S rRNA gene sequences typically found in lakes and the atmosphere. All acquired sequences (319 rain, 296 freshwater, and 529 atmosphere) were initially aligned using the fast_aligner arb tool (Ludwig et al., 2004) before the alignment was heuristically adjusted using primary and secondary rRNA structure as a guide. The Classifier function of the Ribosomal Database Project II (RDP) (Cole et al., 2007) was used to assign rain, freshwater, and air 16S rRNA gene sequences to the RDP taxonomical hierarchy at the phylum and class levels of resolution.

A suite of phylogenetic analysis tools developed by Schloss and colleagues (Schloss & Handelsman, 2005; Schloss & Handelsman, 2006a, b) was used to make comparisons at finer scales of taxonomic resolution. These tools (dotur, sons, and treeclimber) are based on a pairwise genetic distance matrix. In order to maximize the number of alignment positions used when calculating genetic distances, short and nonoverlapping sequences were removed from the original alignment. The reduced data set was comprised of an alignment that was 562 bp in length (Escherichia coli positions 831–1393) containing 310 rain-derived sequences (from this study), 144 freshwater-derived sequences (Zwart et al., 2002; Newton et al., 2006), and 415 atmosphere-derived sequences all from Brodie et al. (2007). All characters in the reduced alignment were used to calculate a distance matrix for input into distance-based operational taxonomic units (OTU) and richness determination (dotur, Schloss & Handelsman, 2005). dotur uses a distance matrix to estimate the number of OTUs corresponding to different levels of sequence identity. The number of OTUs containing rain, freshwater, or both rain and freshwater sequences were recorded from dotur output at a broad range of sequence identities. sons (Schloss & Handelsman, 2006a, b) was used to compare overlap between freshwater, rain, and atmosphere communities using dotur output. sons uses collector's curve extrapolation methods similar to Ace and Chao's richness estimators to predict the proportion of overlap between two or more communities (Schloss & Handelsman, 2006a, b). An additional distance matrix was constructed using the reduced alignment, but was subjected to a 50% base frequency filter with columns containing gaps removed (c. 439 resultant positions) in arb (Ludwig et al., 2004). The filtered distance matrix was used along with treeclimber to determine whether the rain, freshwater, and air sequence libraries share an ancestral community structure (Schloss & Handelsman, 2006a, b). treeclimber estimates a parsimony score from a phylogenetic reconstruction with the tips labeled with their source. How this parsimony score differs from the parsimony scores calculated with randomly assigned sources for each phylogenetic tree tip determines the statistical significance of differences between sampled communities.

Nucleotide sequence accession numbers

16S rRNA gene sequence fragments generated in the current study have been submitted to GenBank under accession numbers EU136733EU137051.

Results and discussion

Temporal variability in deposition rates may be driven by precipitation

The estimated rates of deposition were two orders of magnitude higher during the first hour of precipitation (c. 5.7 × 108 cells m−2 h−1) than during relatively dry conditions (c. 7.3 × 106 cells m−2 h−1). Our estimates of deposition were significantly higher than previous estimates: dry, 5 × 103 to 2 × 104 CFU m−2 h−1 (Lindow & Andersen, 1996); and wet, 2.5 × 106 CFU m−2 h−1 (Lindemann & Upper, 1985). However, the discrepancies are likely because of the underestimation of bacterial cell density from CFU counts. Finally, we found no difference in dry deposition rates between littoral and pelagic sites (T-test, P=0.24, N=20) or across lakes (anova, P=0.54, N=20).

At first glance, atmospheric deposition of bacterial cells (wet c. 5.7 × 108 cells m−2 h−1 and dry c. 7.3 × 106 cells m−2 h−1) seems large and would seem to be a significant contribution to bacterial numbers in lakes. However, if we consider our rates of deposition in a mass balance context, atmospheric deposition over a day only represents 0.0001–0.1% of typical planktonic bacterial stock in a lake (c. 1 × 1012 cells m−3), depending on lake bathymetry and weather conditions. In addition, bacterial production estimates range from 0.1 to 50 μgC L−1 h−1 (del Giorgio & Cole, 1998). Using an estimate of bacterial cell carbon content from Bratbak (1985), this corresponds to roughly 8 × 108–4 × 1012 cells m−2 day−1 (assuming a 1-m-deep epilimnion, Fig. 1). This range encompasses and significantly surpasses our estimates of bacterial deposition from the atmosphere, even during rain events. These estimates also approach estimates of contribution from surface water inlet in lakes with theoretical retention times >1 year (Lindstrom et al., 2006). Both estimates of particle sinking flux from the epilimnion of a lake using Stokes' law (c. 8 × 108 cells m−2 day−1) and empirically determined grazing rates (c. 1 × 109 to 1 × 1014 cells m−2 day−1, again assuming a 1-m-deep epilimnion) (Vaque et al., 1994) remove equal or greater numbers of cells than we estimate to be deposited from the atmosphere. These data suggest that atmospheric deposition does not represent a significant contribution to bacterial cell concentrations in temperate lakes (Fig. 1), and it is unlikely that bacterial immigration can be conceptualized using a mass-effect perspective (Leibold et al., 2004).

Figure 1.

 Potential magnitudes of cell loss and gain to a lake epilimnion. Gray bars indicate gains and black bars indicate cellular losses. Grazing and production are based upon literature values, although reported volumetrically we assume a epilimnetic depth of 1 m for these calculations (Vaque et al., 1994; del Giorgio & Cole, 1998); sinking is an estimate based upon Stokes' law (Nazaroff & Alvarez-Cohen, 2001), and atmospheric deposition rates are from this study. Both sinking and atmospheric deposition are calculated on an areal basis (m−2).

Taxonomic affiliation of bacterial cells deposited in rain

The RDP-defined taxonomic composition of each set of sequences is presented in Fig. 2. Proteobacteria dominated the freshwater and rain libraries, whereas the remaining sequences were variable in their phylogenetic affiliation, across libraries. The atmosphere library contained a large number of sequences derived from Firmicute-related taxa (primarily from the urban site) and Proteobacteria-related taxa (mostly from the rural site). Closer inspection of the Proteobacteria sequences in each data set revealed strong distinctions in Proteobacteria composition across libraries (Fig. 2). The freshwater data set (Zwart et al., 2002; Newton et al., 2006) was dominated by Betaproteobacteria, whereas the rain libraries were dominated by Gammaproteobacteria and the atmosphere libraries were relatively balanced in their proteobacterial class composition (Fig. 2 and Supplementary Table 1).

Figure 2.

 Taxonomic proportions of clone libraries from published freshwater sequences (Zwart et al., 2002; Newton et al., 2006), published sequences from air in San Antonio, TX (Brodie et al., 2007), and rain at two sites (deciduous-dominated canopy and conifer-dominated canopy). Bars represent proportions of only Proteobacteria sequences and colors correspond to the Proteobacteria key. All taxonomic definitions are based on the Ribosomal Database Project II (Cole et al., 2007).

Table 1.   Output from dotur analysis (Schloss & Handelsman, 2005)
dotur% identityRain OTUsAtmosphere OTUsRain OTUs w/FWRain OTUs
w/atmosphere
Atmosphere
OTUs w/FW
  1. The number of OTUs containing rain or atmosphere (Brodie et al., 2007) sequences are reported. The proportion of rain OTUs containing sequences from our freshwater sequence database (FW) (Zwart et al., 2002; Newton et al., 2006) or sequences from the Brodie et al. study are also reported. Finally, overlap of the atmosphere and FW OTUs is presented.

1002133870.000.000.00
99.51503430.000.000.00
991042930.020.010.00
97712270.130.020.01
95571810.180.030.03
9038900.370.150.13
8526500.420.290.24
8017230.760.540.61
70351.000.600.80
67121.000.500.50
61111.001.001.00

Our analysis conducted at a finer taxonomic resolution revealed that the composition of both rain libraries did not contain a large number of sequences traditionally seen in freshwater systems or in the urban atmosphere clone library (Supplementary Table 1). dotur revealed that at 99% and 97% identity only c. 2% and c. 13%, respectively, of the defined rain OTUs contained sequences from our freshwater sequence database (Zwart et al., 2002; Newton et al., 2006). sons estimated that only c. 1% and c. 6% of rain OTUs (at 99% and 97%, respectively) would overlap with these freshwater sequences.

treeclimber confirmed the strong distinctions between the rain libraries and the previously published freshwater sequences or atmospheric sequences. It is highly unlikely that the rain libraries and either the freshwater sequences or the San Antonio air sequences came from the same source community (P<0.0001). Estimated parsimony scores well below the random distribution suggested that as yet unidentified factors have differentially structured the freshwater, air, and rain bacterial communities, as characterized in this study. Notably, it is also highly improbable that the two rain libraries (deciduous vs. conifer canopy) came from the same metacommunity (P<0.0001).

The striking differences in the composition of the libraries constructed from bacterial cells deposited during a rain event and previously observed freshwater libraries suggest that atmospheric dispersal of common freshwater bacterial groups may be more limited than perceived previously (Fenchel, 2003; Sloan et al., 2006). This is not to say that freshwater bacterial taxa are precluded from atmospheric transport. However, our comparison does imply that the majority of cells delivered to freshwater bodies via rain are not typically found in the freshwater body itself. This observation was confirmed by Maron et al. (2005), who observed bacterial 16S rRNA gene sequences, in their atmosphere samples, that are traditionally associated with soil and plants. The strong differences between the two rain libraries and the San Antonio air sequences also suggest that the taxonomic composition of bacteria deposited from the atmosphere is heterogeneous in space, although this is not surprising. This heterogeneity is likely driven by many factors including land cover differences, regional land use patterns, and weather patterns. Further characterization of bacteria dispersed via the atmosphere and their influence on dynamics in recipient environments is necessary. Our findings suggest that deposition could also vary in magnitude temporally in response to meteorological conditions.

The perception that microorganisms are not limited by dispersal and that immigration is a key component of bacterial population dynamics and distribution is widespread in microbial ecology (Baas Becking, 1934; Fenchel, 2003; Fenchel & Finlay, 2004; Sloan et al., 2006). This perception is based on the small cell size, large population sizes, and apparent ubiquity of bacteria (Fenchel & Finlay, 2004); however, little effort has been made to characterize potential routes of immigration by bacteria. Our initial attempt to quantify rates of bacteria cell deposition and characterize the taxonomic composition of bacteria deposited in rain suggests that it is unlikely that atmospheric deposition of bacteria strongly influences aquatic bacterial community dynamics. This is not surprising when one considers the success that researchers have had in explaining patterns of change in bacterial communities with chemical, physical, and biological drivers (Simek et al., 2003; Kent et al., 2004; Jones et al., 2008; Shade et al., 2007).

Our study does not disprove the species sorting (Baas Becking, 1934; Leibold et al., 2004) or neutral (Bell, 2000; Hubbell, 2001; Sloan et al., 2006) perspectives of metacommunity theory, but it does suggest that the influence of atmospheric deposition of bacteria relative to within-system interactions is quite small. The relatively small magnitude of cellular deposition and apparent lack of overlap in composition between freshwater bacterial communities and rain-derived bacteria suggest that immigration via the atmosphere may only represent low-level, stochastic variability that is independent of within-system dynamics. We estimated the contribution of wet and dry deposition relative to the growth rate of bacteria in a lake as (deposition rate/growth rate) × proportion of atmospheric immigrants that are traditionally aquatic. Based on our estimates in this study the relative contribution of atmospheric deposition would range from 4 × 10−8 to 0.09. The low end of this range corresponds to immigration rates during periods with no or low precipitation, high within-system bacterial production, and a stringent definition of bacterial ‘species’; the high end represents extreme levels of precipitation with ‘species’ definitions at low percent identity cutoffs (c. 95–97%). Similar estimates for the relative contribution of inlet streams to the bacterial community of lakes in Sweden would range from 0.02 to 0.81 (Lindstrom et al., 2006). These numbers are roughly analogous to the Neutral Theory's m (Hubbell, 2001; Sloan et al., 2006; Woodcock et al., 2007). Woodcock et al. (2007) recently estimated m to be 10−6 by fitting denaturing gradient gel electrophoresis-based estimates of bacterial community composition in water-filled tree holes to a parameterized version of the neutral model. Although the majority of the assumptions made by the Neutral Theory of Biodiversity are quite controversial, we believe that the immigration term (m) is a useful method for conceptualization of the influence of immigration on recipient bacterial communities. In addition, long-term monitoring of immigrating bacteria via all avenues and within-system bacterial dynamics should be conducted to accurately quantify the relative role of immigration in shaping aquatic bacterial communities.

Acknowledgements

The authors gratefully acknowledge A. Schiller, T. Cadkin, and V. Bauza for technical assistance and H. Allen, N. Broderick, and two anonymous reviewers for comments on earlier versions of this manuscript. We also thank the staff at the University of Wisconsin-Madison Trout Lake Field Station and Center for Limnology for logistical support. This work was funded by the North Temperate Lakes Long-Term Ecological Research site (National Science Foundation DEB-0217533) and the University of Wisconsin-Madison Graduate School.

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