Supplementary material

Figure A1. Map of geographical location of studies about sclerophyllous forest (polygons) and number of studies per ecosystem (color scale). The numbers on the map represent a study, referring to its identification on Supplementary material (Table A1).

Figure A2: Map of area loss of the Coastal Mediterranean sclerophyllous forest of Cryptocarya alba and Peumus boldus, using the criteria of historical decline (A3) and recent decline (A1) (Schulz et al. 2010); for the latter only the area represented by Castillo et al. (2009) study appears in green.

Figure A3. Map of area loss of the Interior Mediterranean sclerophyll psammophytic forest of Quillaja saponaria and Fabiana imbricata using the criteria of historical decline (A3) and recent decline (A1).

Figure A4. Map of restricted distribution (Criterion B) of coastal Mediterranean deciduous forest of Nothofagus macrocarpa and Ribes punctatum using the sub-criteria B1: minimum convex polygon (EOO), B2: cells of 10x10 km used for the analysis (AOO) and B3: number of locations.

Table A1. Description of reviewed studies. The main results, pressures and effects on the ecosystem identified in each publication are shown and the methodology of spatially explicit studies are detailed identifying the sensor or source of data, the software and the type of analysis.

Study Theme Methodology (ES only) Eco-syste

m (ID)*

*Author

Study

time

Type* Results Ecosystem

pressureEcosystem

effectsSensor or

source Software Analysis typeValidation method and

accuracy

Bustamante & Castor,

(1998)

1981-

1991SE

-The Ruil forest (Nothofagus Alessandrii) changed from 827.8 ha to 352,2 ha (deforestation rate of 8,15%).-The sclerophyllous forest was replaced by plantation, which is now the new landscape matrix.

-Tree plantation expansion-Opening of agricultural land through slash and burn of native forest.

-Surface loss-Biomass loss due to burning

Aerial Photos Scale

1:10.000 (SAF)

Arc/Info Photointerpretation in GIS

Not reported 11

Echeverría et al.

(2006)

1975-

2000SE

-Decrease of 65% of native forest extent. The deforestation rate was 4.5%.- Wide fragmentation of native forest; the patches became very small.-Transformation of native forest to scrubs in the period 1074-1990.

- Tree plantation expansion-Forest degradation to scrubland

- Surface loss-Structural degradation of arboreal stratum

Landsat (MMS, TM and ETM+)

ArcView 3.2

Supervised classification and

landscape fragmentation

analysis

Confusion matrix.

Accuracy of each image:

-1975: 82.7%-1990: 83.3%-2000: 84.9%

11, 12, 18 and 19

Castillo et al. (2009)

1986-

2007SE

- 450 ha burned in 1989; 14,872 ha burned in 1986-87.-The burned zones were colonized by invasive species.-The burned zones did not recover their original biomass.

-Roads and the urban-forest border are the main sources of fire in the area.

-Change in the composition to invasive species-Biomass loss due to fire-Surface loss

Landsat (TM) -

Photointerpretation on satellite

images in false color and NDVI to

evaluate fires.

Not reported 8, and 9

Aguayo et al. (2009)

1979-

2000SE

-Loss of 40% in original surface of sclerophyllous scrubland and 28.2% in native forest between 1979 and 2000.

- Tree plantation expansion (rate of +10.5%).- Opening of agricultural land through slash and burn of native forest

- Surface loss

Landsat (MMS and

ETM+)

ArGis 9.0 and

IDRISI 14.02

Supervised classification

Confusion matrix.

Accuracy level not reported

11, 12 and 14

Little et al. (2009)

1975-

2000

SE -Decrease from 52% in the native forest surface in 1975 to 14% in 2000 in Purapel basin, while in Cauquenes change in the same period from 36.1% to 8.1%.- Surface runoff was affected by the expansion

- Exotic plantation.

-Soil quality degradation-Surface loss

Landsat (MMS, TM and ETM+)

ArcView 3.2 and ERDAS

Analysis of the daily flow of watersheds

Stratified random

design by land-use

type.

11, 12, 18 and 19

of plantations; however, this difference was not statistically significant in both basins.- In summer pine plantations reduce runoff (canopy interception and evapotranspiration).

Missing data of stream

flow-17.4% in Purapel

-14%% in Cauqenes

Altamirano & Lara (2010)

1989-

2003SE

- 40% of loss in native forest, while the agricultural area decreased by 49%.-The plantations increased in around 500%, at the expense of agricultural land, scrub and native forest.-Highest levels of deforestation were concentrated between 400 to 1,400 m asl.-The deforestation rate was 4.1%.

- Tree plantation expansion- Forest degradation to scrubland.

- Structural degradation of arboreal stratum- Surface loss

Landsat (TM) and

Aster

ERDAS Imagine

8.4

Supervised classification

Confusion matrix.

Accuracy of each image:-1989: 95%-2003: 92%

12 and 13

Schulz et al. (2010)

1975-

2008SE

-Sclerophyllous scrubland had a loss of 0.7% while the native forest decreased 1.7% (period 1975-2008).- Tree plantations had the highest rate of increase (3.2%) with an increase of 288% in the study period.The highest rate of expansion of tree plantation was between 1999 and 2008 with an 10.6%.-The agricultural surface increased at 1.1% of rate.- The coastal zone was the most dynamic, experiencing up to 3 land cover change in the study period.

- Tree plantation expansion in the coastal zone.-Increase of agricultural areas.-High dynamism of land use and cover change at coastal zone.

- Alteration of ecological succession- Surface loss

Landsat (MMS, TM and ETM+)

and Aster

ArcGis 9.2,

IDRISI Andes

v.15 and Google Earth

Supervised classification y Land Change

Modeler

Confusion matrix and Cohen´s

Kappa Index of

agreement:-1975: 63.4%-1985: 73.8%-1999: 75.8%-2008: 88.3%

3, 5, 6, 7, 8, 9, 10, 11,

12, 15 and 20

Van de Wouw et al, (2011)

1975-

2008SE

-Only the 34,5% of the sclerophyllous forest persisted without undegraded between 1975 y 2008. A 46% of the initial forest was converted into savannas.-The probability of transition to savanna was correlated with slope and aspect in all the period of study.-The regeneration capacity decrease as it moves away from the forest fragments.-Livestock showed no correlation with the step to savannas.- Acacia savannas act as an intermediate state of recovery sclerophyllous forest

-Degradation of forest to savannas due fires and anthropogenic pressures associated with land uses.

- Change in the composition to invasive species- Structural degradation of arboreal stratum- Surface loss

Landsat (MMS, TM and ETM+)

and Aster

ArcView 3.2 and IDRISI Andes v.15

Supervised classification

Confusion matrix and Cohen´s

Kappa Index of

agreement.

The study used the

same images of Schulz et al. (2010).

The accuracy is the same

of that study.

5, 6, 7, 8, 9, 10, 11 and

12

Patterson & Hoalst-

Pullen,

1976-

2003SE

- Identify a pattern of change in land cover, which varies with the harvesting process, for it used the concept of equifinality.

-Forest planting and harvesting process,

- Alteration of ecological succession

Landsat (MMS, TM y

- Supervised classification

No accuracy assessment performed

14

(2011)

- Between 1976 and 1986, forest plantations increased by 10 %, then between 1986 and 2000 increased mature plantings, then between 2000 and 2007 increase base soil.

influenced by social dynamics (i. e D.L 701).

- Surface loss

ETM+) y Aster

Carmona et al.

(2012)

1999-

2009SE

- The study identifies the process of " Afforestation " which had a rate of 2.55 % (expansion of forest plantations)- It also identifies the "substitution" as the change from one use to plantations, this had a rate of 1.23 %.-The forest close roads have high risk of fires.

- Forestal plantation expansion.- Roads as a source of risk of forest fires.

- Change in the composition to invasive species-Increase of phyto-fuel

National Land

Survey of Vegetation (1999) and fuel model

of July (1995)

ArGis 9.3

Autologistic regression and Extensión Land Change Modeler

Overall accuracy of autologistic regressions above 70%.

11, 12 and 13

Nahuelhual et al.

(2012)

1975-

2007SE

-The plantations increased from 17,9% in 1990 to 42,7% in 2007.-The scrubland was the most affected due the expansion of exotic plantation.-Between 1975 y 1990 the plantations occupied slopes from 0 to 15%, then between 1990 and 2007 colonized highest slopes.

- Tree plantation expansion.-Location of plantations in high slopes (> 15 %) increase the risk of erosion.

- Soil quality degradation- Surface loss

Landsat (MMS, TM and ETM+)

IDRISI 3.2

Supervised classification

Confusion matrix

The study used the

same images of Echeverría et al. (2006). The accuracy is the same

of that study

11 and 12

Olivera-Guerra et al. (2014)

2004 and

2006SE

The highest evapotranspiration (ETd) were recorded in forest covers, the lower ranks are present in the coastal dunes and bare soil. Forest plantation have the grates ETd. The forest plantation consumed more water than native covers.

-Tree plantations modify the energy and water balance.

-Aquifer degradation-Changing in energy balance.

MODIS and

ASTER (reflectivit

y and thermal)

-

Energy Balance model for

estimating daily evapotranspiration

This study employed a

95% confidence level (α=

0.05) in all the statistics

process.

11, 12 and 19

Vergara et al. (2013)

1989-

2009SE

Forest surface decrease 61.7% between 1989 and 2009, the number of patches decrease and number of components increase (group of patches).- Connectivity decreased 90% in the time of study-Native forest was replaced by grassland and the urban areas was the principal agent of connectivity decline between components.

-Urban and suburban expansion

-Loss of connectivity- Surface loss

Landsat (TM and ETM+)

PCI Geomatics v. 10.2

Supervised classification y

connectivity analysis

Confusion matrix and Cohen´s

Kappa Index of

agreement. Accuracy level not reported

1, 2, 6, 7, 8, 9

and 20

Hernández et al.

(2015)

1975-

2011

SE -Gain of spinal degraded, urban areas and exotic forest plantations.-Spinals were transformed into agricultural land-There was a recolonization of native forest and scrub on abandoned agricultural land. Expansion rate of 2.1% of native forest.

-Agriculture-Study identified condition of native forest recovery

-Secondary succession after abandonment of agricultural

Landsat (MMS and

TM)

ENVI 4.7 Supervised classification

Confusion matrix

Global accuracy:

-1975: 93%

5, 8 and 9

-The spinal acted enabling connectivity between patches of native forest; they allowed seed dispersal. In this study the native forest showed good recovery.

land-Native forest recovery-Increase in dispersal of propagules

-1992: 91%-2002: 96%-2011: 79%

Ávila et al. (1981)

1978 and

1980EX

-Study found that burning the native seed reduced saplings by half, while exotic seeds increased 36.3%.-The geophytes life forms are less present in burned sites.-Fires altered the composition of ecosystem, benefiting exotic plants that are more adapted to fires than natives. On the other hand providing benefit to the soil providing phosphorus and improving biomass production.

-Forest fires modified the dominance of native vs exotic species.-Exotic species

-Change in ecosystem composition to exotic species domination-Modification of primary productivity by increasing the phosphorus

- - - - 8

Peñaloza et al. (2001)

1991 and

1993EX

-Photosynthetically active radiation (PAR) does not vary between habitats under Kagenekia angustifolia and open sectors.-The nurse effect of K. angustifolia is expressed primarily in the protection of snow. Facilitation effect of other plants improved recruitment plants of other species.-Success depends on rainfall, so its decrease could modify the structure of this ecosystem.

-Variability of precipitation (possibly associated with the effect of climate change) affects plants dependent recruitment of K. angustifolia

-Nurse effect of structural type-Reduction of recruitment by climate change

- - - - 7

Figueroa et al. (2004) 2004 EX

-The establishment of naturalized herbaceous plants in scrub is around 45%.-The seed banks of naturalized herbaceous plants in sclerophyllous montane forest accounted around 55%.-Ulex europaeus inhibits the growth of woody plants in disturbed forests.-Exotic species alter ecosystem functioning and change the structure in the long-term due to modification of resources or nutrients availability.

-Exotic species

- Change in ecosystem composition to exotic species domination-Inhibition of woody plants.-Alteration of seed banks

- - - - 6

Figueroa et al. (2009)

2003 EX - Using soil samples subjected to fire treatment, they identified that 60% of the seeds were from exotic species.- Exotic seeds were the least affected by heat and smoke.

-Exotic species.-It is unclear if fires will benefit native or exotic species, because it

- Change in floristic composition from native to exotic

- - - - 6

- Native seeds responded well to heat (not so high temperatures).- The dominance of native or exotic after a fire depends on complex factors.

depends on factors such as temperature.

species

Gómez-Gonzales

et al. (2009)

2009 EX

-Some native species in close scrubland did not resist burning conditions.-The fire benefited exotic species like T. pratense.-When fire is not intense will not affect the richness of native species.-The abundance of exotic species increase with fire.

-Exotic species-Forest fires.

- Change in ecosystem composition to exotic species domination

- - - - 10

* SE, spatially explicit; EX, experimental studies (these last ones used only as reference information).** Ecosystem ID: 1) Interior mediterranean thorn forest of A. caven and Prosopis chilensis; 2) Andean mediterranean thorn forest of A. caven and Baccharis paniculata; 3) Coastal Mediterranean thorn forest of A. caven and Maytenus boaria; 4) Interior mediterranean thorn forest of A. caven and Lithraea caustica; 5) Coastal mediterranean sclrerophyll arborescent scrub of Peumus boldus and Schinus latifolius; 6) Interior mediterranean sclrerophyll arborescent scrub of Quillaja saponaria and Porlieria chilensis; 7) Andean Mediterranean sclerophyll forest of Kageneckia angustifolia and Guindilia trinervis; 8) Coastal Mediterranean sclerophyll forest of Cryptocarya alba and P. boldus; 9) Coastal Mediterranean sclerophyll forest of L. caustica and C. alba; 10) Andean Mediterranean sclerophyll forest of Q. saponaria and L. caustica; 11) Coastal Mediterranean sclerophyll forest of L. caustica and Azara integrifolia; 12) Interior Mediterranean sclerophyll forest of L. caustica and P. boldus; 13) Andean Mediterranean sclerophyll forest of L. caustica and Lomatia hirsuta; 14) Interior Mediterranean sclerophyll psammophytic forest of Q. saponaria and Fabiana imbricata; 15) Coastal Mediterranean deciduous forest of Nothofagus macrocarpa and Ribes punctatum; 16) Interior Mediterranean deciduous forest of Nothofagus obliqua and C. alba; 17) Andean Mediterranean deciduous forest of N. obliqua and Austrocedrus chilensis; 18) Coastal Mediterranean deciduous forest of Nothofagus glauca and Azara petiolaris; 19) Coastal Mediterranean deciduous forest of N. glauca and Persea lingue; 20) Coastal Mediterranean short scrub of Chuquiraga oppositifolia and Mulinum spinosum.

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