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Landscapes Forest and Global Change - ESA - Escola Superior ...

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P.C. Goebel et al. 2010. How important are riparian forests to aquatic foodwebs in agricultural watersheds<br />

132<br />

Isotope ratios are expressed as δ 13 C <strong>and</strong> δ 15 N values per mille [‰] relative to the international<br />

reference st<strong>and</strong>ard VPDB using NBS 19, L-SVEC, IAEA-N-1 <strong>and</strong> IAEA-N-2. St<strong>and</strong>ards<br />

deviations of δ 13 C <strong>and</strong> δ 15 N replicate analyses were 0.2 ‰ <strong>and</strong> 0.2 ‰, respectively.<br />

DOC samples were analyzed for δ 13 C using an O.I. Analytical Model 1010 TOC Analyzer (OI<br />

Analytical, College Station, TX) interfaced to a PDZ Europa 20-20 isotope ratio mass<br />

spectrometer (Sercon Ltd., Cheshire, UK). This analysis was conducted at the UC Davis Stable<br />

Isotope Facility, in the Department of Plant Sciences. A 20-mL aliquot of sample was<br />

transferred into a heated digestion vessel <strong>and</strong> reacted sequentially with phosphoric acid then<br />

with sodium persulfate to convert DIC <strong>and</strong> DOC each into a pulse of CO 2 . The two sequential<br />

CO 2 pulses liberated by the chemical treatments are carried in a helium flow to an infra-red gas<br />

analyzer (IRGA), then to the isotope ratio mass spectrometer where the 13 C/ 12 C ratios are<br />

measured <strong>and</strong> compared to ratios of laboratory st<strong>and</strong>ards calibrated against NIST St<strong>and</strong>ard<br />

Reference Materials.<br />

We compared δ 13 C <strong>and</strong> δ 15 N values of dominant basal resources (autotrophs <strong>and</strong> detrital<br />

materials) between forested <strong>and</strong> non-forested streams using a t-test. Likewise, to examine<br />

differences in stable isotope signatures for macroinvertebrate functional feeding groups <strong>and</strong><br />

dominant fish species between forested <strong>and</strong> non-forested riparian areas, we also utilized a t-test.<br />

3. Results<br />

We detected no statistically significant differences in δ 13 C values of dominant autotrophs <strong>and</strong><br />

detrital material between forested <strong>and</strong> non-forested streams (Figure 1A). Algae δ 13 C values were<br />

the most depleted, ranging from -40.5‰ to -22.3‰ while δ 13 C values of the epilithon were the<br />

most enriched (ranging from -23.3‰ to -15.1‰), followed by FPOM δ 13 C values (ranging from<br />

-23.0‰ to -11.3‰). With values ranging collectively from -32.5‰ to -23.6‰, δ 13 C values of<br />

CPOM, riparian vegetation (tree <strong>and</strong> herbaceous), <strong>and</strong> macrophytes were similar (Figure 1A.).<br />

We did detect significant differences in δ 15 N values of basal resources (Figure 1A).<br />

Specifically, we found that macrophytes <strong>and</strong> CPOM were enriched in the non-forested sites<br />

compared to the forested sites (t-test; P = 0.01 <strong>and</strong> 0.01, respectively). No differences in δ 15 N<br />

values of the other autotrophs or detrital material were detected between forests <strong>and</strong> nonforested<br />

riparian areas.<br />

Overall, consumer δ 13 C values across all species are best characterized as enriched, with δ 13 C<br />

values ranging between -28.0‰ <strong>and</strong> -20.2‰ <strong>and</strong> δ 15 N values between 3.2‰ to 8.5‰ for all<br />

macroinvertebrate functional feeding groups (Figure 1). Both filterers <strong>and</strong> grazers had higher<br />

δ 15 N values associated with non-forested riparian areas than forested riparian areas (t-test; P =<br />

0.01 <strong>and</strong> 0.02, respectively). Similarly, δ 13 C values ranged from -22.0‰ to -26.2‰ <strong>and</strong> δ 15 N<br />

values from 10.5‰ to 12.7‰ for selected fish species, with creek chubs having significantly<br />

more enriched δ 13 C values in the non-forested riparian areas (t-test; P = 0.01). These values are<br />

similar to the values for FPOM, CPOM, <strong>and</strong> riparian plants (Figure 1).<br />

4. Discussion<br />

Our results, which were only collected once <strong>and</strong> do not capture seasonal variation in isotopic<br />

signatures, suggest that there are not marked differences in the primary sources of energy<br />

supporting aquatic food webs among forested <strong>and</strong> non-forested headwater streams in this<br />

agricultural watershed. Neither the primary consumers (e.g., grazers) nor higher-level<br />

consumers (e.g., black-nose dace) showed differences in δ 13 C signatures among forested <strong>and</strong><br />

<strong>Forest</strong> <strong>L<strong>and</strong>scapes</strong> <strong>and</strong> <strong>Global</strong> <strong>Change</strong> -New Frontiers in Management, Conservation <strong>and</strong> Restoration. Proceedings of the IUFRO L<strong>and</strong>scape Ecology<br />

Working Group International Conference, September 21-27, 2010, Bragança, Portugal. J.C. Azevedo, M. Feliciano, J. Castro & M.A. Pinto (eds.)<br />

2010, Instituto Politécnico de Bragança, Bragança, Portugal.

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