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Tomas F. Domingues, Joseph A. Berry, Luiz A. Martinelli, Jean P. H. B. Ometto, and James R. Ehleringer

1. Introduction The Amazon rain forest has been recognized as a major component of the global energy budget and the cycling of carbon, nutrients, and water ( Dickinson 1989 ; Lean and Warrilow 1989 ; Shukla et al. 1990 ; Malhi and Grace 2000 ; Cramer et al. 2004 ). An emerging consensus points to the Amazonian rain forest as a dynamic ecosystem changing in response to today’s global changes ( Phillips et al. 2004 ). Because of the global significance of this biome, it is important to answer

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Michael Keller, Ruth Varner, Jadson D. Dias, Hudson Silva, Patrick Crill, Raimundo Cosme de Oliveira Jr., and Gregory P. Asner

the carbon balance of logging at the Tapajos National Forest using field measurements of damage and simple models of decay, regrowth, and off-site carbon loss to predict carbon budgets following logging ( Keller et al. 2004b ). To account for regrowth following logging, we integrated fluxes over 30 yr assuming single harvesting entries, a new harvested area each year, and simulated regrowth following logging. For a 30-yr integration under RIL management we predicted a loss of 1500 kg CO 2 ha −1

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Lydia P. Olander, Mercedes M. Bustamante, Gregory P. Asner, Everaldo Telles, Zayra Prado, and Plínio B. Camargo

along the east side of the Tapajós River at 02°50′S latitude, 55°00′W longitude. The TNF is underlaid by old alternating sand and clay lacustrine sediments with the water table located 60–140 m below the surface ( Williams et al. 2002 ). The logging area varies between 150–200 m ASL and is minimally bisected by drainages. The soils are 70% clay dominated (ultisols and oxisols) and 30% sand dominated (ultisols; Silver et al. 2000 ). Mean annual temperature is 25°C and rainfall averages 2000 mm yr −1

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