After logging, the mean canopy openness was 19.2% in CNV (n=9 plots) and 13.3% in RIL (n=8 plots), and the distributions of the canopy class in RIL and CNV significantly different (χ2=43.56, P<0.001).
This study aimed to correlate logging intensity with canopy opening using medium-resolution satellite images (SPOT-type) on a sample of 15 blocks totaling more than 3300 ha in two French Guianan forests with different reliefs.
It is consistent with post-logging canopy gaps that boost growth but is greater than what is observed in undisturbed forests in central Africa (0.15 0.20 cm yr −1 on average).
Before logging, mean canopy openness in CNV (three plots only) and RIL (9 plots) was similar (3.6 and 3.1%) and not significantly different (χ2=2.73, P=0.254).
It appeared that the total abundance of seedlings did not differ significantly between logging gaps and natural canopy gaps.
General linear models (glm) were created to test the relationship between canopy damage, logging intensity and relief at local scales (1 and 4 ha) and at the management unit scale (i.e. 200 300 ha).
Comparisons of canopy cover before and after harvesting indicate little change in canopy cover when logging slash is considered, indicating that logging slash affected energy balances within the streams.
Most studies on the carbon balance of selectively logged forests have estimated pre- and post-logging carbon stocks with remote sensing methods [16], allowing large-scale estimation of logging extent and quantification of canopy damage [14, 17, 18].
At the block scale, a 20% canopy opening after logging was observed for a logging intensity of 3.5 trees ha−1.
This study aims to identify the impact of RIL on the regeneration of commercial timber species by comparing the regeneration dynamics of logging gaps with naturally occuring canopy gaps.
Activities that induce forest degradation include fire, logging, fuelwood extraction, and sub-canopy grazing and cultivation [15].
